# European Red List of Habitats Table

Habitat Description:
These are shallow to very shallow temporary pools, existing only in winter and early spring, and seasonally wet depressions, mostly oligotrophic, in the Mediterranean and warm Atlantic part of Europe, and in Northern Africa.  They are colonised by pioneer ephemeral freshwater vegetation with above-ground growth visible for only a short part of the year,  just 1-3 months. The predominant life forms are annual amphiphytes (Mediterranean spring annuals/therophytes), germinating in the aquatic phase and reproducing in the terrestrial ecophase, such as species of Juncus, Lythrum and Elatine or semi-terrestrial geophytes such as species of Isoetes and Serapias. Ephemeral vegetation types constituted by these plant species occur on water-saturated or submerged acidic sands or calcium rich soils, which completely dry out in spring. In some cases ephemeral vegetation is also developed in the flush habitats on rock outcrops, where seasonal surface runoff creates temporarily wet conditions in the patches of rock debris. The communities are classified in the order Isoetalia, covering the alliances Isoetion, Cicendion, Lythrion tribracteati, Preslion cervinae and Agrostion salmanticae. This habitat is very important for invertebrates (especially branchiopods and dragonflies) and amphibians (newt and frogs, like species of Triturus, Bufo, Rana and Hyla).
Indicators of quality:
• Distinct vegetation zonation related to the water level fluctuations
• Natural hydrological regime of the catchment with no significant hydrological impact by e.g. water extraction as indicated by pipes, dams, removal of soil/gravel and with conditions adequate for the survival and persistence of typical species
• High insolation of the habitat without excessive shading by scrub or forest vegetation
• Relative abundance of Mediterranean annual and geophytic species
• Substrate with no excessive disturbances (e.g. excessive trampling)
• Clear water with no eutrophication
• Absence of evidence(s) of primary or secondary succession (e.g. encroachment of shrubs, tall helophytes) and or floating species (pleuston)
• No garbage and waste dumping
• No impact of pesticides and pollutants
• Not significant presence of nitrophilous or ruderal species or invasive neophytes
Characteristic species:
Vascular plants: Aira elegantissima, Agrostis pourretii, Baldellia ranunculoides, Bellis annua, Briza minor, Centaurium maritimum, C. spicatum, Chaetopogon fasciculatus, Callitriche brutia, C. truncata, Cicendia filiformis, Crassula tillaea, C. vaillantii, Crypsis aculeata, C. alopecuroides, Cyperus michelianus, Damasonium alisma, D. bourgaei, D. polyspermum, Elatine gussonei, E. macropoda, Eryngium corniculatum, Exaculum pusillum, Herniaria glabra, Illecebrum verticillatum, Isoetes duriei, I. heldreichii, I. azorica, I. histrix, I. setacea, I. velata, Isolepis setacea, Juncus bufonius, J. capitatus, J. foliosus, J. pygmaeus, J. tenageia, Lotus conimbricensis, L. angustissimum, L. parviflorus, Lythrum castellanum, L. flexuosum, Lythrum thymifolia, L. tribracteatum, Marsilea batardae, M. strigosa, Mentha cervina, M. pulegium, Nananthea perpusilla, Ophioglossum lusitanicum, Pilularia minuta, Ranunculus batrachioides, R. dichotomiflorus, R. lateriflorus, R. muricatus, R. revelieri, R. trilobus, Serapias cordigera, S. lingua, S. neglecta, S. vomeracea, Sisymbrella aspera, Solenopsis corsica, S. laurentia, S. minuta.
Bryophytes: Calliergon cuspidatum, Drepanocladus fluitans, Eurhynchium striatum, Riccia spp.,
Fauna : Amphibians : Salamandra spp, Triturus spp, Discoglossus spp, Alytes spp., Pelobaates spp, Pelodytes punctatus, Pelodytes ibericus, Bufo spp, Hylas pp, Rana perezi, Rana kl. grafi. Branchiopods: Branchypus spp, Chirocepalus spp, Linderiella massiliensis, Streptocephalus spp, Tanymastigites spp, Lepidurus apus, Triops cancriformis, Cyzicus spp, Imnadia yeyetta.

Classification:
EUNIS:
C1.6 Temporary lakes, ponds and pools
Annex I:
3120 Oligothrophic waters containing very few minerals generally on sandy soils of the West Mediterranean, with Isoetes spp.
3170* Mediterranean temporary ponds
EuroVegChecklist alliances:
Isoetion Br.-Bl. 1935
Cicendion (Rivas Goday in Rivas Goday et Borja 1961) Br.-Bl. 1967
Lythrion tribracteati Rivas Goday et Rivas-Mart. in Rivas Goday 1970
Preslion cervinae Br.-Bl. ex Moor 1936
Agrostion salmanticae Rivas Goday 1958
Emerald:
C3.4 Species-poor beds of low-growing water-fringing or amphibious vegetation
MAES:
Fresh water, Rivers and lakes
IUCN:
5. Wetlands (inland)
5.8.Seasonal/Intermittent Freshwater Marshes/Pools

Justification Outstanding Example of Biogeographical Region:
This habitat is dependent upon a Mediterranean climate so is confined to that region.

Map Description:
The map is rather complete for EU28, but data gaps outside EU28 in Croatia, Montenegro and Albania. Data sources: Art17, NAT.

Comment EU28:
Territorial data also show 108km2 for Portugal transfered from C1.6b

Trends in Quantity:
Present past trend in quantity (over the past 50 yrs) is estimated >21 % for both EU28 and EU28+. Long historical trend in quantity is fundamentally unknown. The future trend is decreasing in most of the countries where it is reported.

Trends in Quality:
The present trends in quality shows an important extent (54%) and severity (50%) of degradation for the six countries which provided information (Croatia, Cyprus, France, Italy and Spain). The historical trend is unknown but it can be estimated as decreasing as consequence of water quality degradation, decreasing phytoceonotic diversity and altered hydrological functioning in the last centuries. A future decline in quality can be reasonably predicted as consequence of a increase of soil and water nutrients.

% of Distribution of the Habitat Type within the EU 28:
About 50%, since this habitat type is known from the south side of the Mediterranean Basin (Morocoo, Algeria, Tunisia) and it is probably also present in the Near East.

Justification of Small Range/Regression:
The habitat occur through the Mediterranean basin.

Justification of Restricted Area:
The habitat occurs in relatively small spots across a wide range.

Pressures and Threats:
The human induced changes in hydraulic conditions is the most significant threat affecting this habitat. Other significant threats are related to water pollution, intensive grazing, roads construction, and urbanisation. A continuing declining of habitat quality is expected where anthropogenic influences are significant. Climate change is also a threatening factor for this habitat.

Conservation and Management:
The main measures for the conservation of this habitat type include maintaining the natural hydrological regime of the catchment avoiding water pollution and eutrophication. It is also very important to maintain sustainable agricultural uses in order to avert the encroachment by shrubs and overgrazing of the habitat. Legal protection of habitats and species, urban and industrial water waste management, and planning of urbanisation and transportation and service corridors are essential in order to preserve this habitat.

Conservation Status:
Annex 1
3120: ATL U2, MED U1
3170: ATL U1, CON U2, MAC U1, MED U1

Capacity to Recover its Typical Character and Functionality?:
Restoration is possible only with the reconstruction of the necessary hydrological and soil conditions.

Summary:
These shallow seasonal pools dependent on winter and early spring retention of rain-water in hollows on acidic or base-rich substrates, have a scattered occurrence through Mediterranean countries with greater abundance westwards. Characterised by pioneer ephemeral vegetation and semi-terrestrial geophytes and with a rich associated fauna, they are vulnerable to the transformation of the hydrological conditions, land exploitation, agricultural use such as overgrazing and urbanisation. Restoration is dependent on the recovery of natural hydrological values and maintainance of sustainable and traditional agricultural uses but may be feasible in the long term.

References:
Bagella S., Gascón S., Caria M.C., Sala J., Mariani M.A., Boix D. (2010) Identifying key environmental factors related to plant and crustacean assemblages in Mediterranean temporary ponds. Biodiversity and Conservation 19: 1749-1768.
Bergmeier, E. (2001): Seasonal pools in the vegetation of Gavdos (Greece) - in situ conservation required. Bocconea 13: 511-516.
Deil, U. (2005). A review on habitats, plant traits and vegetation of ephemeral wetlands - a global perspective. Phytocoenologia 35 (2-3): 533-705.
Grillas, P., Gauthier, P., Yavercovski, N. & Perennou, C. (2004). Mediterranean Temporary Pools; Volume 1 – Issues relating to conservation, functioning and management. Station Biologique de la Tour du Valat.
Pinto-Cruz C., Molina J.A., Barbour M., Silva V. & M.D.(2009) Espírito-Santo. Plant communities as a tool in temporary ponds conservation in SW Portugal. Hydrobiologia 634: 11-24.

Criterion A Text:
Values for A1 were calculated from quantitative territorial data sheets of six EU28 and one EU28+ countries. Overall an average trends of -21% from EU28 countries and -21% from EU28+ countries over about 50 years were calculated. A long historical trend is unknown for almost all the countries. Quantitative estimation trends in future are decreasing for Spain, France and  Italy,  the countries with the highest contributions to habitat surface in Europe.

Criterion B Text:
The EOO, AOO and number of locations are far beyond the thresholds for critera under B, and therefore other subcriteria for B have not been assessed.

Criterion C/D Text:
The overall extent and severity are the weighted average calculated from reported data from France, Greece, Italy, Spain, Croatia and Cyprus. The involved countries could not provide any information on long historical or future trends in quality (CD2, CD3, C2, C3, and D2). The changes in quality includes both abiotic and biotic  indicators, so C/D1 has not been split into C1 and D1. On average there is a decrease in quality affecting 54% of the surface with an average severity of 50%.

Synthesis:
The habitat type is assessed as Vulnerable (VU) because of a strong decline in quality over the last 50 years (criterion C/D1) both at the EU28 and the EU28+ levels. In quantitative trems 54% of the extent of the habitat is negatively affected with a 50% of relative severity. Additionally, there is a strong decline in area (-21%), but not large enough to meet the threshold for Near Threatened.

Sub-habitats in Need of Examination:
Mediterranean temporary waters with Isoetes can be considered as a sub-habitat type in which further examination might be required at a regional level.

Contributors:
Habitat definition: P. Dimopoulos.
Territorial data: O. Argagnon, J. Capelo, D. Espírito-Santo, C. Pinto-Cruz, J.A. Molina, A. Lumbreras, E. Agrillo, F. Attorre, S. Bagella, L. Casella, D. Gigante, G. Giusso Del Galdo, C. Marcenò, G. Pezzi, S. Sciandrello, D. Viciani
Working Group Freshwater Habitats: G. Arts, F. Landucci, J.A. Molina, B. Poulin, H. Toivonen


Habitat Type Name:
H2.6a Temperate, lowland to sub-montane base-rich scree

Habitat Description:
Mostly coarse, unstabilized, dry, sunny, calcareous and marble screes of the colline and montane levels of the low- to mid-altitude levels of the temperate European reliefs, including the piedmonts of the Alps, Jura, Pyrenees, Carpathians and Hercynian ranges. They are located on the slopes of mountains, hills, but also in gorges. The vegetation can completely lack, but in other cases is represented by forb- or fern- dominated communities. The main plant species are Achnatherum calamagrostis, Melica ciliata, Galeopsis angustifolia, Rumex scutatus, Vincetoxicum hirundinaria and the ferns Gymnocarpium dryopteris. The fern swards colonize often slightly damp parts of screes. Other species in these more mesophilous screes are Eupatorium cannabinum, Valeriana officinalis, Galeopsis ladanum. The vegetation mostly belongs to the alliances Stipion calamagrostis and Arabidion alpinae. The plant communities of calcareous screes of the Paris basin and its periphery (Leontodontion hyoseroidis) have many rare or endemic plants, like the endangered endemic Viola hispida. The screes of the Eastern Carpathians are characterized by the presence of numerous sub-Mediterranean thermophilous species and some Balkan-Carpathian subendemics, which penetrate northwards from the south to the sunny and warm habitats. Carpathian endemics on screes in Romania are amongst others Silene nutans subsp. dubia and Thymus comosus. Similar communities can occur on secondary substrates, like quarries. 
Indicators of quality:
The following characteristics may be considered as indicators of good quality:
•    natural erosion processes
•    absence of non-native species (e.g. Robinia pseudacacia may support the processes of stabilisation of screes and extinction of the typical flora)
•    presence of habitat rare, endemic and relict species
•    absence of human activities, like grazing.
Characteristic species:
Flora 
Vascular plants: Achnatherum calamagrostis, Aethionema saxatile, Anthericum ramosum, Arabis alpina, Biscutella neustriaca,  Calamagrostis varia, Campanula rapunculoides, Cardaminopsis arenosa, Cystopteris fragilis, Eupatorium cannabinum, Euphorbia waldsteinii, Galeopsis angustifolia, Galeopsis ladanum, Galium timeroyi subsp. fleurotii, Gymnocarpium robertianum, Festuca xanthina, Hieracium bifidum, Iberis durandii, I. violetii, Lamium garganicum subsp. laevigatum, Leontodon hyoseroides, Linaria supina, Melica ciliata, Microrhinum minus, Moehringia muscosa, Parietaria officinalis, Poa nemoralis, Rumex scutatus, Senecio rupestris, Sesleria albicans, Scrophularia juratensis, Silene hayekiana, Silene nutans subsp. dubia, S. vulgaris subsp. glareosa, Sisymbrium supinum, Silene nutans subsp. dubia, Thymus comosus, Vincetoxicum hirundinaria, Valeriana officinalis, Viola hispida. Mosses: Ceratodon purpureus, Conocephalum conicum, Eurhynchium schleicheri, Homalothecium sericeum, Mnium stellare, Plagiomnium affine, Tortella tortuosa.

Classification:
EUNIS:
H2.6 Calcareous and ultra-basic screes of warm exposures
EuroVegChecklist:
Stipion calamagrostis Jenny-Lips ex Br.-Bl. 1948
Leontodontion hyoseroidis Duvigneaud et al. 1970
Arabidion alpinae Beguin 1972
Annex 1:
8160* Medio-European calcareous scree of hill and montane levels
Emerald:
H2.6 Calcareous and ultra-basic screes of warm exposures
MAES-2:
Sparsely vegetated land
IUCN:
6. Rocky Areas [e.g. inland cliffs, mountain peaks

Justification Outstanding Example of Biogeographical Region:
No. This habitat type occurs frequently in the alpine region, but it is also well distributed – though scattered - in the continental and atlantic biogeographical regions.

Map Description:
The map is relatively complete for the EU, with missing points in the Cantabrian mountains, but incomplete in the Balkan and Switzerland. Data sources: Art17, NAT.

Comment EU28:
Important missing data from Italy. Data from Poland and Bosnia-Herzegovinia are not included due to late arrival of data.

Comment EU28+:
Important missing data from Italy. Data from Poland and Bosnia-Herzegovinia are not included due to late arrival of data.

Trends in Quantity:
The current trends are reported as stable in most countries. The past trend over the last 50 years is on average slight at the EU scale (-12% EUR28+; -9% EUR28). The same trend calculated with the upper limits of ranges – when provided – reaches -20% for EU28+ and -17% for EU28. Reported changes are variable among countries, reflecting a variable level of knowledge and/or perception. Austria, Germany and Switzerland have reported quite higher values than other countries. The average trend seem nevertheless realistic. The decline is mainly caused by human activities such as quarrying and the construction of transportation infrastructures. The decrease in quantity is also be caused by the natural process of scree stabilization and subsequent natural succession (encroachment). The historical decrease has been reported with the same pattern (no precise figure is available). The future trend is said to be stable or slightly decreasing (no precise figure is available).

Trends in Quality:
The decrease in quality over the last 50 years is on average more than simply local (extent 12% EUR28, 30% EUR28+) and the changes are fairly significant (severity 30% EUR28, 26% EUR28+). The reported values are rather consistent among countries. Therefore, the calculated trend may be considered realistic. This reduced quality is mainly due to a loss of functionality of screes (reduced mobility), which is caused by nearby quarries and constructions or by natural succession. Natural succession is faster at lower elevation than up the mountains (cf. H2.4 type). Roads often go across screes and reduce their mobility by cutting the slow flow of scree materials (stones). Erosion and alteration of cliffs above screes release materials regularly; any securing of such cliffs prevents screes from functioning normally. Sheep grazing, which is reported as a threat in Ireland and UK, also affects the quality. Problems of invasive species are reported in Ireland (Epilobium brunescens, a plant introduced from New Zeland).  Historical and future trends cannot be described owing to a lack of data.

% of Distribution of the Habitat Type within the EU 28:
95%. The native biota (especially plants) has a narrow distribution from a world point of view. The entire distribution is inside EU28+ countries, except a very small part in Ukraine.

Justification of Small Range/Regression:
No. The natural range of this habitat type is large (well above 50,000 Km² threshold) and no important decline has occurred during the last 50 years.

Justification of Restricted Area:
This habitat type occurs only a small spots in the lowlands and low mountains, when habitat conditions are appropriate. I does have an intrinsically restricted area.

Pressures and Threats:
Human-induced and natural-processes-dependent threats are of equal relevance for this habitat. Human-induced threats comprise quarrying of natural sites with cliffs and screes, and the constructions of transportation infrastructure. Of less concern are sheep grazing in (Ireland and the UK) and outdoor activities (creation of trails across screes). The natural process of scree stabilisation is responsible for the encroachment and natural afforestation of stabilized screes (natural succession); it is reported as the main threat in Germany.

Conservation and Management:
There is no management need for this highly natural habitat to remain but leaving it undisturbed and undamaged. Natural succession should not be considered as a problem because it is not human-induced. Conservation is then effective when free evolution is possible, like within protected areas. ‘Manage landscape features’ refers to the need to better protect this kind of habitats showing a high degree of naturalness in land-use planning, especially when no other specific regulation can be applied (no protected species or habitat, outside a protected area, outside a N2000 site).

Conservation Status:
Annex I:
8160: ALP FV, ATL U2, CON U1, PAN FV

Capacity to Recover its Typical Character and Functionality?:
The habitat has some capacity to recover naturally but it is dependent on some geomorphological processes which are very slow (erosion). As far as we know, there is no experiment of restoration of screes.

Summary:
This habitat comprises screes of mostly coarse, unstabilized material derived from calcareous and dolomitic bedrocks in the lowlands, foothills and sub-montane zone of  temperate Europe. Vegetation can be completely lacking, but rock surfaces can have bryophyte and lichen communities and, where crevices accumulate soil, the vascular contingent can be diverse and lush. Natural succession following stabilization of screes allows encroachment of shrubs and trees, vegetation not included here. The habitat is widely threatened by quarrying and the construction of transport infrastructures, and by leisure activities. Quality is also affected by sheep grazing in some regions. Such situations need careful pastoral management.

References:
Duvigneaud, J., Durin, L., Mullenders W. 1970 La végétation des éboulis de Pagny-la-Blanche-Côte (Meuse, France).Vegetatio, 20 (1-4) : 48-73.
Sadlo, J. 2009. Svaz SCA Stipion calamagrostis Br.-Bl. et al. 1952. In: Chytry, M. (ed.). Vegetacy Czeske Republiky. 2. Ruderalni, plevelova, skalni a sufova vegetace. Praha Academia: 452-461.
ValachoviÄ, M., Dierssen, K., Dimopoulos, P., HadaÄ, E., Loidi, J., Mucina, L., Rossi, G., Valle Tendero, F., Tomaselli, M. 1997. The vegetation on screes - survey of higher syntaxa in Europe. Folia Geobot. Phytotax. 32: 173-192.

Criterion A Text:
The values given above were calculated with the territorial data only. The lower and upper limits of decrease are the following : EUR28+ [-6/-20%], EUR28  [-4/-17%].

Criterion C/D Text:
The values were calculated with the territorial data of a large subset of countries providing data on the reduction in quality. This allowed for the calculation of a realistic trends. The ranges of degradation of quality lead to the conclusion Least concern for EU28 and EU28+.

Synthesis:
This habitat type qualifies for a Least Concern status, both for EU28 and EU28+ because average trends in quantity and quality are slight. Looking at the upper limit of decrease – the worst decrease – calculated with the data (around -20% over the last 50 years), the Nearly Threatened category could be assigned with justification, but quality, consistency and completeness are not sufficient enough to do so.

Contributors:
Habitat definition: Rossen Tzonev
Territorial data: M. Chytrý, R. Delarze, L.-M. Delescaille, P. Finck, C. Gussev, J. Loidi, V. Matevski, A. Mikolajczak, D. Paternoster, P. Perrin, U. Raths, U. Riecken, A. Ssymank, M. ValachoviÄ
Working Group Sparsely Vegetated Habitats: F. Essl, G. Giusso del Galdo, A. Mikolajczak, D. Paternoster, M. ValachoviÄ, M. Valderrabano


Habitat Type Name:
H3.2c Temperate, lowland to montane base-rich inland cliff

Habitat Description:
This habitat type includes calcareous or base-rich rock faces and crevices in lowland to montane belts of European mountains in the temperate bioclimatic region.  Plant species growing on these rocks are adapted to extreme habitat conditions, such as strong solar radiation, a low water content, strong fluctuations in day/night and seasonal temperature, strong winds, absence of snow cover, and poorly developed soil. However, the conditions in lower altitudes are not as severe as in high altitudes (habitat H3.2b): radiation is lower, many species grow in more shady places, the fluctuation of temperature is not so extreme, and winds are less strong. Despite this, many endemic and rare species occur in these habitats. 
On more sunny rocks we can find communities of the order Potentilletalia caulescentis, namely in the Central and Easter Alps and Western Carpathians from the alliance Potentillion caulescentis and in the Southern Carpathians from the Micromerion pulegii. On more shady rocks communities from the order Violo biflorae-Cystopteridetalia alpinae appear, in the Southern Dinarides the alliance Edraianthion and in the rest of Europe the alliance Violo biflorae-Cystopteridion alpinae.
Indicators of quality:
Many endemic and legally protected species occur in this habitat. The main threats are air pollution, exploitation of limestone, intensive tourism (climbing), grazing, collecting of flowers, erosion, natural destruction of the rocks.
The following characteristics may be considered as indicators of good quality:
•    occurrence of natural erosion processes,
•    species richness of the cliffs and presence of the characteristic species,
•    presence of rare species at their typical frequency.
Characteristic species:
Flora:
Vascular plants: Androsace lactea, Asplenium fontanum, A. ruta-muraria, A. scolopendrium, A. trichomanes, A. viride, Campanula cochlearifolia, C. cespitosa, C. rotundifolia, Cardaminopsis arenosa subsp. borbasii, Carex brachystachys, Ceterach officinarum, Cystopteris fragilis, Draba aizoides, D. norvegica, D. sauteri, Erinus alpinus, Hieracium amplexicaule, H. bupleuroides, H. humile, Globularia cordifolia, Kernera saxatilis, Moehringia muscosa, Polypodium interjectum, Potentilla caulescens, Rhamnus pumila,Valeriana montana, V. tripteris.

Classification:
EUNIS:
H3.2 Basic and ultra-basic inland cliffs
EuroVegChecklist:
Potentilletalia caulescentis Br.-Bl. in Br.-Bl. et Jenny 1926
Potentillion caulescentis Br.-Bl. In Br.-Bl. et Jenny 1926
Micromerion pulegii Boscaiu (1971) 1979
Violo biflorae-Cystopteridetalia alpinae Fernandez Casas 1970
Violo biflorae-Cystopteridion alpinae Fernandez Casas 1970
Edraianthion LakušiÄ‡ 1968
Annex 1:
8210 Calcareous rocky slopes with chasmophytic vegetation
Emerald:
H3.2 Basic and ultra-basic inland cliff
MAES-2:
Sparsely vegetated land
IUCN:
6 Rocky areas [e.g. inland cliffs, mountain peaks]

Justification Outstanding Example of Biogeographical Region:
This habitat type has a widespread distribution across several biogeographic regions.

Map Description:
The map is incomplete for the Balkan. Data sources: Art17, NAT.

Trends in Quantity:
The current trends in quantity have been reported as stable in most countries, except in Switzerland, Bulgaria and Slovakia (slight decreasing trend). There has been a slight decline in quantity over the last 50 years (-5% EU28+; -4% EU28), which is mainly caused by quarrying that simply destroys cliffs and rock outcrops. The reported changes are variable among countries, reflecting a variable level of knowledge and different contexts. The average trend seems nevertheless realistic. The strongest decrease in quantity is reported in Germany (-25/-30%). Taking into account the ranges of values given by some countries, the lower rate of decline in EU28+ would be 2% and the upper 7%. The historical and future trends are stable or slightly decreasing, but no precise figures are available.

Trends in Quality:
A recent decrease in quality has occurred quite locally (extent -7 and -12% in EU28 and EU28+) with a limited severity of degradation (28 and 35% in EU28 and EU28+). The reduction in quality is largely due to the alteration of and disturbance to the native biota of base-rich cliffs. Outdoor activities (rock climbing, mountaineering and via ferrata) affect this habitat type due to the cleaning of routes (removing of plants and unstable rocks from itineraries) and by disturbing wildlife. Biocenotic evolution of surrounding habitats (grasslands, scrublands, and forests) brings shade to cliffs and therefore, causes changes in the habitat conditions. The securing of cliffs for security reasons affects this habitat type in pretty the same way as outdoor activities do. A lack of data from important Eastern countries (e. g. Poland) does not allow to say how changes vary across the EU. There is a lack of data to assess historical and future changes. However, lowland countries with few base-rich cliffs, such as Germany, Belgium or Lithuania, tend to report worse severity and extent of degradation.

% of Distribution of the Habitat Type within the EU 28:
95 %. The native biota (especially plants) have a narrow distribution from a worldwide point of view. The entire distribution lies inside EU28+ countries, except a very small part in the Ukraine.

Justification of Restricted Area:
Compared to high-mountain regions, this habitat type occurs naturally only on small spots in the lowlands and low mountains when habitat conditions are appropriate. So it does have an intrinsically restricted area (of occurrences).

Pressures and Threats:
The main threat is quarrying that simply destroys this habitat. Secondary threats are outdoor activities, biocenotic evolution and securing of cliffs, which rather cause changes in quality than in quantity. Outdoor activities (rock climbing, mountaineering, via ferrata) affect this habitat type due to the cleaning of routes (removing of plants and unstable rocks from itineraries) and by disturbing wildlife. Biocenotic evolution of surrounding habitats (grasslands, scrublands, and forests) brings shade to cliffs and therefore, causes changes in habitat conditions. The securing of cliffs for security reasons affects this habitat type in pretty the same way as outdoor activities do. The threats are more significant in northern or lowland countries (i.e. non-Mediterranean countries) where this habitat type is much more scattered, which makes it more sensitive to these threats. Problems of invasive species are reported in Ireland (Epilobium brunnescens, a plant originating from New Zealand).

Conservation and Management:
Cliffs are highly natural elements of the mountain environment and of hills dominated landscapes. Therefore, the conservation of this habitat type does not require a specific management but leaving it undisturbed and undamaged. Conservation is effective when free evolution is possible like within protected areas. Unless protected species or habitats are present, the conservation of cliffs is not taken into account in construction projects and land-use planning. In France, natural areas managers mainly seek cooperation with other stakeholders such as climbers and gliders to better control these activities and make people aware of the disturbances they may cause to plants and animals (prevention) instead of segregative conservation approaches.

Conservation Status:
Annex 1 types:
8210: ALP FV, ATL XX, BLS U1, BOR U1, CON U1, MED XX, PAN FV

Capacity to Recover its Typical Character and Functionality?:
At least for plants, natural recovery of this habitat is rather fast when it is not isolated from habitats of the same type. However, the return of specialized nesting birds after strong disturbances, for example, is less easy.

Summary:
This habitat type includes calcareous or base-rich rock faces and crevices in the lowland to montane belts of European mountains in the temperate region. Though conditions are not so severe as at higher altitudes, plant species growing on these rocks are adapted to extreme habitat conditions, such as strong solar radiation, a low water content, strong fluctuations in day/night and seasonal temperature, strong winds, absence of snow cover, and poorly developed soil. Many endemic and rare species occur here. Losses have been mainly due to quarrying but quality is affected by eisure activities such as rock-climbing and mountaineering that often go along with the cleaning and securing of cliffs. Those activities also affect the behaviour of animal behaviour, such as breeding birds.

References:
Horvat, I., GlavaÄ, V. and Ellenberg, H., 1974. Vegetation Südosteuropas. Gustav Fischer Verlag, Stuttgart. 
Mucina, L., 1993. Asplenietea trichomanis. In: Mucina, L. and Grabherr, G. (eds.), Die Pflanzengesellschaften Österreichs. Teil II. Natürliche waldfreieVegetation. Gustav Fischer Verlag, Jena. 
Oberdorfer, E., 1977. Süddeutsche Pflanzgesellschaften. Teil I. Gustav Fischer Verlag, Jena.

Criterion A Text:
The values given above were calculated with the territorial data only, using average values in case ranges were provided. Using the maximum values, the calculated reduction would be 7% (EU28+) and 6% (EU28). Using the minimum values, the calculated reduction would be 3% (EU28+) and 2% (EU28).

Criterion C/D Text:
The values were calculated with the territorial data. They can be regarded as reliable because eleven countries out of thirteen reported on recent changes in quality.

Synthesis:
The overall Red List status is Least Concern (LC). Decreases in quantity and quality are well below the thresholds to qualify for the Near threatened category. Despite a variable data quality among countries and a lack of important data from Eastern countries, the calculated trends reflect somewhat the reality and, therefore, the assessment can be considered as reliable.

Sub-habitats in Need of Examination:
Cliffs oustide moutain regions (i.e. in the lowlands) should be assessed separetely beacause they show a larger decrease in quality compared to lowland cliffs within calcareous mountains.  Indeed, threats concentrate on a much small

Contributors:
Habitat definition: N. Juvan & A. ÄŒarni.
Territorial data: E. Agrillo, S. Armiraglio, S. Assini,  F. Attorre, J. Bölöni, G. Buffa, L. Casella, M. Chytrý, R. Delarze, L.M. Delescaille, P. Finck,  D. Gigante, C. Gussev, J. Loidi, A. Mikolajczak, D. Paternoster, P. Perrin, V. RašomaviÄius, U. Raths, U. Riecken, A. Ssymank, M. ValachoviÄ, D. Viciani.
Working Group Sparsely Vegetated Habitats: F. Essl, G. Giusso Del Galdo, A. Mikolajczak, D. Paternoster, M. ValachoviÄ, M. Valderrabano


Habitat Type Name:
A5.47: Communities of Mediterranean lower circalittoral (shelf-edge) detritic bottoms or open-sea detritic bottoms

Habitat Description:
This habitat develops on a mixture of gravel sediments, sand and mud. The fine part of the mix appears in a greater proportion than in the sediments that support the coastal detritic biocenosis. The gravel, mainly organogenic, is largely formed by calcareous debris of quaternary thanatocenoses. The open-water detritic bottoms normally belong to the lower circalittoral and constitute the deepest layer of the circalittoral zone on soft bottoms. These communities are present in detritic bottoms with abundance of dead shells, bryozoans and coral skeletons. This habitat hosts a biocenosis of great diversity and abundance. The high production of plankton at the shelf break makes it an important feeding ground for large shoals of fish and cetaceans. Some facies of the edge of the platform, such as the one made by the crinoid Leptometra phalangium, increase the structural complexity of the habitat enhancing the abundance and species richness. They also host a high abundance of spawners of commercially important species, e.g. Red Mullet (Mullus barbatus), Hake (Merluccius merluccius), Blue Whiting (Micromesistius poutassou) and Trisopterus minutus capelanus. Thus, the conservation of shelf-edge habitat is also important with a view to reducing the fish mortality in the sensitive phases (recruitment, spawning, postspawning) of the life cycle of demersal fish species.
 
Indicators of quality:
Both biotic and abiotic indicators have been used to describe marine habitat quality. These include: the presence of characteristic species as well as those which are sensitive to the pressures the habitat may face; water quality parameters; levels of exposure to particular pressure, and more integrated indices which describe habitat structure and function, such as trophic index, or successional stages of development in habitats that have a natural cycle of change over time.
There are no commonly agreed indicators of quality for this habitat, although particular parameters may have been set in certain situations, e.g. protected features within Natura 2000 sites, where reference values have been determined and applied on a location-specific basis. 
Characteristic species:
Characteristic species include: Pelecypoda: Pinna rudis, Astarte sulcata, Chlamys clavata, Pseudamussium clavatum; Scaphopoda: Dentalium panormitanum, Antalis panorma; Bivalve: Limopsis aurita; Decapoda: Ebalia granulosa; Malacostraca: Lophogaster typicus; Amphipoda: Haploops dellavallei; and Echinoderms: Ophiura carnea and Thyone gadeana. Species present also include Holothuria forskali, the teleost Gobius quadrimaculatus and the brachiopod Gryphus vitreus. Sometimes the following species can also be found: the bivalve Venus casina, Pseudamussium clavatumâ€‹ and Astarte sulcata, the irregular sea urchin Spatangus purpureus, and the brittle star Ophiacantha setosa. Some species of filter feeders like the sea pen Funiculina quadrangularis or the actinian Actinauge richardii are also very abundant in this type of community.

Classification:
EUNIS (v1405):
Level 4.  A sub-habitat of ‘Mediterranean circalittoral mixed sediment’ (A5.4)
 
Annex 1:
No relationships.
 
MAES:
Marine - Shelf 
 
MSFD:
Shelf sublittoral mixed sediment
Shelf sublittoral coarse sediment
 
EUSeaMap:
Shelf coarse of mixed sediments
 
 
IUCN:
9.4 Subtidal sandy
9.5 Subtidal sandy-mud

Map Description:
There are insufficient data to provide a comprehensive and accurate map of the distribution of this habitat. This map has been generated using EMODnet data from modelled/surveyed records from the Mediterranean (and supplemented with expert opinion where applicable) (EMODnet, 2015). EOO and AOO have been calculated on the available data presented in this map however these should be treated with caution as expert opinion is that this is not the full distribution of the habitat. Distribution information is available only from the western Mediterranean although the habitat type is known to be widespread in the Mediterranean Sea.

Trends in Quantity:
The distribution of this habitat is still poorly known, and the studies conducted have mostly focused on the description of the benthic assemblages in relation to sediment characteristics. There are a few reports that have highlighted a reduction in the abundance of epibenthic organisms of this habitat, particularly on beds with L. phalangium such as those on the north coast of Crete (Greece), at Heraklion Bay in the southern Aegean or in the southern Tyrrhenian Sea as a result of otter- and other fishing trawling impacts. In Heraklion Bay for example, a 80% reduction of the beds of L. phalangium over last 60 years has been estimated. However, trends in other regions are unknown.

Trends in Quality:
There are no concrete studies that evaluate the trends in quality over the last 50 years, and no information on past and future trends has been given by territorial experts. Nonetheless, expert opinion indicates a decrease in the habitat quality from slight to moderate in the western Mediterranean, Adriatic and Italian Central Mediterranean area. At fishing trawled sites in the Sicilian Channel or the Thryrrenian Sea, different species and abundance of fauna has been found in comparison with nearby untrawled areas, with a higher abundance of epifaunal scavengers and motile burrowing infauna, and lower abundance levels of structuring fauna such as crinoids and ophiuroids in those areas where trawling has been occurring. Thus, a reduction in the quality of the habitat has occurred at some sites.

% of Distribution of the Habitat Type within the EU 28:
The habitat is widely distributed in the Mediterranean Sea but it is not possible to provide an estimation of the habitat area that lies within the EU 28.

Pressures and Threats:
Trawling and dredging fishing are the most important factors influencing the structure of both benthic and demersal assemblages of this habitat. The impact of towed gear is particularly heavy on some sub-habitats, such as the ones containing the crynoid Leptometra phalangium, a fragile organism that is easily removed by trawling. Other epibenthic organisms have shown reduced abundance in trawled areas.

Conservation and Management:
Basic knowledge on the habitat and its distribution in the Mediterranean, its species assemblages, its species biology (distribution, abundance, habitat preferences, life cycles) and monitoring data on trends is needed to improve spatial planning in general, and strategic planning of particular human activities. Monitoring of spatial distribution of fishing effort is also recommended.
Designation of Marine Protected Areas (MPA) and Fisheries Restricted Areas (FRAs) in sites where this habitat occurs, particularly where Leptometra phalangium, Neolampas rostellata and Ophiacantha setosa occur, should be established to create a representative network of Mediterranean MPAs. This will also help to control the fishing effort, especially the establishment of closed areas over part of the distribution of this habitat to protect juvenile and spawning fish and fragile benthic communities.

Conservation Status:
Annex 1: 
No relationships.
 
Included in the Council of Europe Bern Convention Res. No. 4 1996 as Sublittoral soft seabed (code 11.22).
Included in the Barcelona Convention (1998) as Biocenosis of shelf-edge detritic

Capacity to Recover its Typical Character and Functionality?:
Leptometra phalangium is typical of the most productive and species-rich shelf-edge environments and easily disturbed by trawling. Individuals are fragile and suffer a strong impact due to demersal trawling (by removal and death). Their reduction might also affect other components of the community and increase fish mortality rates in crucial life history stages of fishes, such as juveniles and spawners. It is unknown how easily these communities can recover, particularly if fishing activities do not stop.

Summary:
This habitat is found at depths between 90 and 250 m creating a belt at the level of the continental slope. The sediment is formed by a bioclastic mixture of gravel, sand and mud according to the historical factors and hydrodynamics of the area. This habitat hosts a biocenosis of great diversity and abundance. The high production of plankton at the shelf break makes it an important feeding ground for large shoals of fish and cetaceans. Some facies of the edge of the platform such as the one made by the crinoid Leptometra phalangium, increase the structural complexity of the habitat enhancing the abundance and species richness. They also host a high abundance of spawners of commercially important species, e.g. red mullet Mullus barbatus, hake Merluccius merluccius, blue whiting Micromesistius poutassou and Trisopterus minutus capelanus. Thus, the conservation of shelf-edge habitat is also important with a view to reducing the fish mortality in the sensitive phases (recruitment, spawning, postspawning) of the life cycle of demersal fish species.
Trawling and dredging fishing are the most important factors influencing the structure of both benthic and demersal assemblages of this habitat. The impact of towed gear is particularly heavy on some sub-habitats, such as the ones containing the crynoid Leptometra phalangium, a fragile organism that is easily removed by trawling. Other epibenthic organisms have shown reduced abundance in trawled areas. Conservation and management should include the establishment of Marine Protected Areas (MPAs) and regulation of fishing, particularlyt trawling with the establishment of closed areas over part of the distribution of this habitat to protect juvenile and spawning fish and fragile benthic communities. Further monitoring would also be beneficial to improve understanding of its distribution and abundance.

References:
Ardizzone, G. 2006. An introduction to Sensitive and Essential Fish Habitats identification and protection in the Mediterranean Sea, Rome
Bellan-Santini, D., Bellan, G., Bitar, G., Harmelin, J. G. and Pergent, G. 2002. Handbook for interpreting types of marine habitat for the selection of sites to be included in the national inventories of natural sites of conservation interest, United Nations Environmental Programm, 217pp
Colloca, F., Carpentieri, P., Balestri, E. and Ardizzone, G. D. 2004. A critical habitat for Mediterranean fish resources: shelf-brak areas with Leptometra phalangium (Echinodermata: Crinoidea). Marine Biology 145: 1129-1142.
De Juan, S., Thrush, S.F. and Demestre, M. 2007. Functional changes as indicators of trawling disturbance on a benthic community located in a fishing ground (NW Mediterranean Sea). Marine Ecology Progress Series 334: 117–129.
Emig, C. C. 1985. Distribution et syndicologie des fonds a Gryphus vitreus (Brachiopoda) en Corse. Marine Biology 90: 139-146.
Gofas, S., Salas, C., Rueda, J.L., Canoura, J., Farias, C. and Gil, J. 2011. Mollusca from a species-rich deepwater Leptometra community in the Alboran Sea. Scientia Marina 78(4).
Mangano, M. C., Kaiser, M. J., Porporato, E. M. D. and Spanò, N. 2013. Evidence of trawl disturbance on mega-epibenthic communities in the Southern Tyrrhenian Sea. Marine Ecology Progress Series 475: 101-117.
Smith, C. J., Papadopoulou, K. N. and Diliberto, S. 2000. Impact of otter trawling on an eastern Mediterranean commercial trawl fishing ground. ICES J. Mar. Sci.: J. Cons. 57 (5): 1340–1351.
Smith, C.J., Banks, A.C., and Papadopoulou, K.-N. 2007. Improving the quantitative estimation of trawling impacts from side scan sonar and underwater video imagery. ICES Journal of Marine Science, 64: 1692-1701
Terribile, K., Evans, J., Knittweis, L. and Schembri, P. J. 2016. Maximising MEDITS: Using data collected from trawl surveys to characterise the benthic and demersal assemblages of the circalittoral and deeper waters around the Maltese Islands (Central Mediterranean). Regional Studies in Marine Science, 3, 163-175.
Tunesi L. and Diviacco G. 1997. Observations by submersible on the bottoms off shore Portofino Promontory (Ligurian Sea), Atti XII Congr. A.I.O.L. (Isola di Vulcano, 18-21 Settembre 1996), Vol.1, 61-74.

Criterion A Text:
There is not information available on past and future trends of this habitat type. Therefore, this habitat has been assessed as Data Deficient under Criterion A.

Criterion B Text:
This habitat has a large natural range in the Mediterranean. The precise extent is unknown however as EOO >50,000km2 and AOO >50, this exceeds the thresholds for a threatened category on the basis of restricted geographic distribution. Trends in quantity are unknown but it is thought that there are some declines in quality in the EU 28 at least and there is no information on whether a threatening process is likely to cause declines in the next 20 years and it is not possible to calculate locations. The distribution of the habitat is such that the identified threats are unlikely to affect all localities at once. This habitat has therefore been assessed as Least Concern under criteria B1(a, c) B2 (a, c) and B3 and Data Deficient for all other criteria.

Criterion C/D Text:
Trawling is affecting this habitat at different locations and expert opinion indicates a slight to moderate decline on the quality of the habitat in the last 50 years, although the extent of the degradation is unknown. As there is insufficient data from most Mediterranean regions, the habitat type is assessed as Data Deficient under Criterion C/D1.

Synthesis:
This is a very poorly studied habitat type and only few reports exist on its distribution, with only a description of the composing communities along some EU Mediterranean countries available. Moreover, data on quality or quantity is lacking and territorial data is not available for much of its distribution range. Several scientific reports highlighted however the impact due to demersal trawling activities. Althought this habitat has a large Extent of Occurrence (EOO) and Area of Occupancy (AOO), and therefore qualifies as Least Concern under criterion B, the habitat is assessed as Data Deficient both at the EU 28 and EU 28+ levels because of the lack of information on its trends in quantity and quality.

Sub-habitats in Need of Examination:
Particular attention is needed for the sub-habitat with abundant Leptometra phalangium, which is increasingly perceived as the habitat of an exceptionally diverse benthic fauna that is easily disturbed by trawling.

Contributors:
Pietro Catrense, S., Smith, C. J. and Papadopoulou, N.


Habitat Type Name:
C3.5b Periodically exposed shore with stable, mesotrophic sediments with pioneer or ephemeral vegetation

Habitat Description:
This habitat type is found along the periodically emergent shorelines of rivers, on exposed bottoms of permanent lakes and ponds, in wetlands at the edges of arable lands and rarely in ephemeral flush habitats. In rivers and lakes, the timing of exposure of their shoreline depends on the precipitation seasonality and on the time of snowmelt. This habitat type includes also artificial ponds drained in summer in intervals of several years as a part of their management. This habitat type must not be confused with Mediterranean vernal pools, which are instead included in the habitat type C1.6b. The habitat types here considered is characterized by pioneer ephemeral vegetation developing especially in summer and autumn. Plants growing in these environments are mainly annual, low-growing and competitively weak species from various families. Well-represented genera include Cyperus, Elatine, Juncus, Ranunculus, Spergularia and Veronica. Vegetation is usually short and open, and its cover increases with successional stage. Some stands are dominated by single species while others are co-dominated by several species. In some cases, especially on exposed pond bottoms and on river shores, the successional stage with short-growing ephemeral wetland species is followed, especially after water draw-down, by a stage with tall-growing annuals such Bidens, Chenopodium, Persicaria and Rumex maritimus. This succession results in a change of this habitat type into the habitat type C3.5a.
Indicators of good quality:
Occurrence in natural environments such as shores of unregulated rivers, natural lakes, pools or ephemeral flush habitats
Occurrence of rare wetland species
Absence or low incidence of competitive, tall-growing and nutrient-demanding wetland herbs
Absence or low incidence of neophytes

Vascular plants: Blackstonia acuminata, Carex bohemica, Centaurium pulchellum, Centunculus minimus, Cerastium dubium, Coleanthus subtilis, Corrigiola littoralis, Cyperus fuscus, C. michelianus, Elatine alsinastrum, E. hexandra, E. hydropiper, E. orthosperma, E. triandra, Eleocharis acicularis, E. ovata, Fimbristylis annua, Glinus lotoides, Gnaphalium uliginosum, Gnaphalium luteo-album, Gypsophila muralis, Hypericum humifusum, Illecebrum verticillatum, Isolepis setacea, Juncus bufonius, J. bulbosus, J. capitatus, J. ranarius, J. sphaerocarpus, J. tenageia, Koenigia islandica, Limosella aquatica, Lindernia procumbens, Ludwigia palustris, Lythrum hyssopifolia, L. tribracteatum, Mentha pulegium, Montia arvensis, Myosurus minimus, Plantago major subsp. intermedia, Potentilla norvegica, P. supina, Pulicaria vulgaris, Pycreus flavescens, P. glomeratus, Radiola linoides, Ranunculus flammula, R. lateriflorus, R. ophioglossifolius, R. sardous, Sagina apetala, S. nodosa, Samolus valerandi, Schoenoplectus supinus, Solenopsis minuta, Spergularia echinosperma, S. kurkae, S. rubra, Tillaea aquatica, Verbena supina, Veronica anagalloides, V. catenata, V. scardica
Bryophytes: Anthoceros agrestis, A. punctatus, Leptobryum pyriforme, Physcomitrella patens, Physcomitrium eurystomum, P. pyriforme, P. sphaericum, Riccia cavernosa, R. ciliifera, R. crystalline, R. huebeneriana 
Vertebrates: Rana spp., Bombina spp., Bufo spp., Triturus spp., Hyla spp., Natrix natrix, N. tessellata, N. maura, Sterna albifrons, S. hirundo, Charadrius dubius, Himantopus himantopus, Recurvirostra avosetta, Vanellus vanellus.
Macroinvertebrates: Nematodes, Lumbricus spp., Hirudo medicinalis, H. troctina, H. verbana, Planorbis spp., Unio spp., Anodonta spp., Lepidurus apus, Triops cancriformis, Anostraca.

Classification:
EUNIS:
C3.5 Periodically inundated shores with pioneer and ephemeral vegetation                             
C3.7 Unvegetated or sparsely vegetated shores with non-mobile substrates
EuroVegChecklist:
Nanocyperion Koch 1926
Radiolion linoidis Pietsch 1973
Elatino macropodae-Damasonion alismatis de Foucault 1988
Eleocharition soloniensis Philippi 1968
Verbenion supinae SlavniÄ‡ 1951
Annex 1:
3130 Oligotrophic to mesotrophic standing waters with vegetation of the Littorelletea uniflorae and/or of the Isoeto-Nanojuncetea
Emerald:
C3.51 Euro-Siberian dwarf annual amphibious swards
MAES-2:
Fresh water, Rivers and lakes
IUCN:
5.6.  Seasonal/Intermittent Freshwater Lakes [over 8 ha]
5.8.  Seasonal/Intermittent Freshwater Marshes/Pools [under 8 ha]

Justification Outstanding Example of Biogeographical Region:
The habitat is wide distributed in Europe and depends mainly by the alternation of wet and dry conditions and physic-chemical characteristic of the soil. This habitat type becomes more rare in southern Europe where the dry period can be too long.

Map Description:
Map is incomplete, but the distribution of Annex I-type 3130 provides potential distribution for the EU28. Coastal sites should be excluded, as they belong to B-types. Data gaps exist particularly in the Balkan, and possibly for Norway. Data sources: Art17, EVA, GBIF, NAT.

Comment EU28:
Only 33% of the countries in which the habitat is expected to occur provided the total area

Comment EU28+:
Only 30% of the countries in which the habitat is expected to occur provided the total area

Trends in Quantity:
Only about 30% of the countries provided some data or information about the trends in quantity of the habitat. The habitat has decreased during the last 50 years in most of the countries. Only Lithuania and Netherland reported that the habitat is currently stable, while in Belgium it is even increasing due to a better management compared to the past of fishpond systems. All the other countries reported a decrease of the habitat between 10 and 80% with a total trend in quantity estimated between 18 to 36% in EU28 and 21 to 37% in EU28+.

Trends in Quality:
Almost all countries that provided data reported a negative trend in quality for the last 50 years with 20 to 90% of the habitat surface in each country affected by a slight to severe degradation. The trend in quality for whole Europe resulted in a relative severity of degradation of 47% affecting 49% of the total extent of the habitat. The general trend has been calculated on around 30% of the countries in which the habitat is supposed to occur (only those countries that provided quantitative data). Currently the habitat results to be stable in some countries such as Finland, Czech Republic and Lithuania.

% of Distribution of the Habitat Type within the EU 28:
The current distribution of the habitat type worldwide is difficult to calculate. Probably around 70% of this habitat type in Europe lies within the EU28. The rest is across EU28+ countries. However the same or very similar habitat types can be found in countries outside EU28 and EU28+ like Russia, Ukraine, Belarus, Turkey, etc.

Justification of Small Range/Regression:
The natural range of the habitat (EOO) is quite extended and probably far to go below 50,000 Km2.

Justification of Restricted Area:
The geographical range of the habitat is quite extended.

Pressures and Threats:
The pressures for this habitat are mainly represented by anthropogenic factors, which induce modification of the water regime or alteration of the soil physical and chemical conditions. Most frequent issues are related to the increase of trophy level and the accumulation of organic sediments that lead this habitat to evolve in the habitat “C3.5a Periodically exposed shores and muddy banks, mainly eutrophic sediments with pioneer and ephemeral vegetation characterized by abundant biomass production”. Other pressures are represented by all those activities that lead to an alteration of the hydrologic regime such as fish farming (here in particular summer drainage restriction), removal of sediments, water abstractions, but also abandonment of the management of water bodies and wet arable fields. The climate change, especially the prolonging of the dry periods, is also a very important cause of local reduction of this habitat. The invasion of this habitat by non-native flora and fauna species is also rather frequent problem that however often follow or come together with other alterations of the habitat like eutrophication.

Conservation and Management:
The conservation and management should include actions leading to a correct management of water abstraction, agricultural and industrial activities in the surrounding and fish farming. The restoration and improvement of the water quality and hydrological regime of fishponds, natural pools and river beds may be necessary in those cases where the habitat is damaged. Such habitat can be in contact with crops, or developing in water bodies used as water supplies for agricultural purposes. In such cases the habitat could be favoured by adopting sustainable crops, limiting the use of fertilizers and biocides, rather than intensive crops.

Conservation Status:
Annex 1 type:
3130: ALP FV, ATL U1, BLS FV, BOR U1, CON U2, MAC U1, MED U1, PAN U1, STE FV

Capacity to Recover its Typical Character and Functionality?:
The capacity of this habitat to recover naturally differs according to the type of damage that the habitat has undergone. If the damage is due to eutrophication or pollution, that is the most common case, the habitat difficulty can recover naturally. In these cases intervention through removal or substitution of polluted soil should be done. Removing the polluted soil and the causes of pollution the habitat can be restored in relatively short time, 10 years. If the soil seed bank is removed from the water body, intervention through reintroduction of species could be necessary.

Summary:
This habitat type is found throughout the European lowlands along periodically emergent shorelines of rivers, on exposed bottoms of lakes and ponds, in wetlands at the edges of arable lands, rarely in ephemeral flush habitats, and in artificial ponds that are periodically drained in summer. In rivers and lakes, the timing of exposure of the shoreline depends on the precipitation seasonality and on the time of snowmelt. The habitat is characterized by pioneer ephemeral vegetation of low-growing, weakly competitive plants developing in summer and autumn. The main threats are natural succession where drying continues, eutrophication and introduction or changes in the management of water bodies. Whenever the habitat is damaged it can be restored through proper management actions tailored to favor the alternation of wet and dry periods and to limit the eutrophication of the sediments.

References:
Deil, U. 2005. A review on habitats, plant traits and vegetation of ephemeral wetlands – a global perspective. Phytocoenologia 35: 533–706.

Criterion A Text:
According to the calculation performed on the data available (around 30%) the reduction in quantity resulted to be between 17 to 33% in EU28 and 19 to 34% in EU28+. This means that there is a wide uncertainty about the current status of the habitat, which may be considered in the categories Least Concern to Vulnerable. Further uncertainty of this result is due to the total area of the habitat reported for France. This value seems to be very high compared with that one reported by neighboring countries. Considering the large lack of data and the uncertain degree of the status it was chosen - based on expert knowledge - to follow a preservative approach considering the habitat Vulnerable (VU) according to criterion A.

Criterion C/D Text:
The reduction in biotic and abiotic quality over the last 50 years affected 50% of the extent of the habitat with a severity of 44% in both EU28 and EU 28+ countries. The calculation is based on data provided by only 30% of the countries in which the habitat is expected to occur. According to criterion C/D the habitat is Near Threatened, however an underestimation or overestimation of the reduction in biotic and abiotic quality may be due to the large gap of data. The calculation is very close to the Vulnerable category.

Synthesis:
The data available for the assessment represent only around the 30% of the countries in which the habitat is expected to occur. Some countries reported a wide range of trend in quantity which causes uncertainty in the average trend of the habitat (criterion A1), with values ranging between Least Concern (LC) and Vulnerable (VU). Using these uncertain data, the habitat has been assessed as Vulnerable, taking into account trend in quality (criterion C/D1), with values very close to the thresholds of Vulnerable.

Sub-habitats in Need of Examination:
Most of the vegetation communities and characteristic species composing this habitat type have limited distribution ranges, and geographical subtypes may be distinguished, which are likely to be more threatened than the habitat in the whole of Europe.<

Contributors:
Type description: M. Chytrý, with contributions by F. Landucci, G. Arts, J.A. Molina, B. Poulin, H. Toivonen
Territorial data: D. Paelinckx, J.-M. Couvreur, K. Šumberová, T. Kontula, G. Király, J. Brophy, A. ÄŒarni, N. Juvan, J.A. Molina, E. von Wachenfeldt, R. Delarze, A. Ssymank, P. Finck, U. Raths, U. Riecken, E. Agrillo, F. Attorre, S. Bagella, L. Casella, C. Giancola, D. Gigante, G. Giusso Del Galdo, C. Marcenò, D. Viciani, H. Mäemets, A. Mikolajczak, V. RašomaviÄius, E. Weeda, Å½. Škvorc, Ä. MilanoviÄ‡, J. Rodwell
Working Group Freshwater Habitats: G. Arts, F. Landucci, J.A. Molina, B. Poulin, H. Toivonen


Habitat Type Name:
C3.5d Unvegetated or sparsely vegetated shore with mobile sediments in montane and alpine regions

Habitat Description:
The habitat includes the bed and banks of rivers and streams from alpine to mountain (and partially sub-montane) belts and of the northern boreal area. The habitat is highly dynamic because it is characterized by periodical floods and frequent and considerable variation of speed and intensity of the water current, which however remains always rather high.  The sediment of the habitat includes mainly gravel deposits and banks of alluvial material, characteristically poor in organic materials and nutrients. The vegetation types occupying these gravel deposits include pioneer vegetation and subsequent early stages in the colonization sequence, with plants  specialised to survive in this habitat, having narrow leaves and elastic stems adapted to or tolerant of submersion and rapid changes of the water current: for example Myricaria germanica, and species of Epilobium Salix, Agrostis, Elimus, Poa.  An important feature is that the vegetation stays in its pioneer stage and is ephemeral but eventual succession leads to willow scrub.
Indicators of good quality:
Natural hydrological cycle of spates
Suitable geological substrate which is easily erodible
High water velocity
Pioneer vegetation with absence or sporadic abundance of nitrophilous species
No high abundance of exotic invasive species
No negative anthropogenic influence (gravel extraction, regulation of the water regime, construction of artificial banks)

Characteristic species:
Vascular plants:  Agrostis gigantea, Arabis alpina, Astragalus alpinus, Calamagrostis pseudophragmites, C. stricta, Cerastium alpinum, Chaerophyllum hirsutum,, Chondrilla chondrilloides,Deschampsia alpina, D. cespitosa,Epilobium roseum, E. fleischeri, E. dodoneii, E. latifolium, Equisetum variegatum,   Erigeron acer ssp. angulosus,Festuca vivipara, Gnaphalium uliginosum,  Hieracium staticifolium, Hippophae rhamnoides, Luzula spicata, Lotus corniculatus, Myricaria germanica,Myosoton aquaticum, Myosotis scorpiodes, Oenanthe crocata,  Ptychotis saxifraga,  Petasites hybridus, P. kablikianus, Poa  trivialis, Poa palustris, Ranunculus repens, Rumex scutatus, Stellaria nemorum, Saxifraga aizoides, Scrophularia canina, Trifolium saxatile, Usually only juveniles or small shrubs of Salix daphnoides, S. elaeagnos, S. lapponum, S. hastata, S. glauca, S. myrsinifolia, S. phylicifolia, S. purpurea, Elymus fibrosus, Elymus transbaicalensis, Elymus kronokensis subsp. subalpinus, Cotoneaster cinnabarinus, Papaver lapponicum, P. dahlianum.
Bryophytes: Brachytecium rivulare, Bryum intermedium, B. klinggraeffii, Ceratodon purpureus, Dichodontium pellucidum, Hygrohypnum luridum, H. ochraceum, Hypnum lindbergii, Pohlia drummondii, P. fillum, Polytrichum juniperinum, Pseudoleskea incurvata, Racomitrum canescens s.l., Tortella inclinata, T. tortuosa.
Lichens: Rhizocarpon spp. (yellow lichens on rocks)
Macroinvertebrates: Larval stages of Odonata, Ephemeroptera, Plecoptera and Trichoptera characterize the benthic communities of riverbeds while nymph and adult stages of the same species can be found on the river banks. Other characteristic species are Ancylus fluviatilis, Pisidium casertanum, Unio crassus, Crenobia alpina, Hyles hippophaes, Proserpinus proserpina.
Vertebrates: Castor fiber, Arvicola sapidus, Myotis blythii, Locustella fluviatilis, Sterna hirundo, Riparia riparia, Burhinus oedicnemus, Coracias garrulous, Anthus campestris, Milvus migrans. Ardeids, breeding passerine and migrating waders can also occur.

Classification:
EUNIS:
C3.5 Periodically inundated shores with pioneer and ephemeral vegetation
EuroVegChecklist (alliances):
Epilobion fleischeri G. Br.-Bl. ex Br.-Bl. 1950
Calamagrostion pseudophragmitis Rivas-Mart. et al. 1984
Calamagrostion neglectae Nordhagen ex de Molenaar 1976
Annex 1:
3220 Alpine rivers and the herbaceous vegetation along their banks
3230 Alpine rivers and their ligneous vegetation with Myricaria germanica
3240 Alpine rivers and their ligneous vegetation with Salix elaeagnos
Emerald:
C3.55 Sparsely vegetated river gravel banks
C3.62 Unvegetated river gravel banks
MAES-2:
The habitat is a freshwater habitat, in the category of rivers and lakes and within this category is categorized in inland surface water (water courses and bodies).
IUCN:
5.2.  Seasonal/Intermittent/Irregular Rivers/Streams/Creeks
WFD:
R-A1, R-A2, R-E1

Justification Outstanding Example of Biogeographical Region:
This habitat is typical of Alpine and Boreal areas of Europe. It also occurs in the high mountains of Atlantic, Continental and sporadically Mediterranean areas.

Map Description:
Map is rather complete for EU28, but  incomplete for EU28+, especially in the Balkan, and with potential distribution in Norway. Data sources: Art17, EVA, NAT.

Trends in Quantity:
During the last centuries the habitat has undergone  a relatively high reduction in quantity (34-36% in the last 50 years and 43-45% since 1750) due to rapidly increasing urbanization and development of agriculture and industrial activities. However several countries (France, Finland, Italy and Switzerland) reported that the habitat is currently stable. There are not sufficient data to make conclusions about the general future trend in Europe, because in some countries the urbanization is still increasing (e.g. Balkan countries).

Trends in Quality:
Paradoxically the trend in quality, compared to the trend in quantity, during the last 50 years has not been so important. This because human actions on this habitat have always deeply modified the structure and functionality of the habitat up to complete transformation into a different habitat type. In Europe around 31% of the habitat extent has been degraded with a relative severity of 33%. There are not sufficient data available to distinguish between the reduction in abiotic and biotic quality of the habitat, and neither are there sufficient data to assess historic and future trends in quality.

% of Distribution of the Habitat Type within the EU 28:
Around 70% of the habitat type lies within EU 28. The remaining part is within EU 28+ countries (Balkan countries) and in the Caucasus. The vegetation of the alliance Muerbeckiello-Epilobion Belonovskaya et al. 2013 is typical of Caucasian river gravel bars.

Justification of Small Range/Regression:
The natural range of the habitat (EOO) is quite extensive and probably far beyond 50,000 Km2.

Justification of Restricted Area:
The geographical range of the habitat is quite extensive and the habitat does not have intrinsically restricted area.

Pressures and Threats:
The main pressures are constituted by those human actions that lead to modifications of the hydrologic regime and functioning of the watercourse. Construction of dams and barriers for energy production, water supply and/or protection of populated areas in the valleys are very frequent. Sand and gravel extraction have represented a common problem for this habitat until now. However during the last years some countries like Italy introduced restrictions of sediment extraction along rivers to limit coastal erosion. Solid and chemical pollution represent another very frequent threat for watercourses. This habitat, when disturbed by human activities, is subject to easy invasion by pioneer exotic plants that sometimes can even become dominant. Climate change represent a potential threat for the habitat because it can cause the permanent alteration of the water regime.

Conservation and Management:
Regulations enacted to limit sediment extraction and water pollution are now common in most European countries. However the expansion of urban areas and anthropogenic activities makes it difficult to reach the right compromise between habitat conservation and the satisfaction of human needs (exploitation of water resources and protection of populated areas). Nevertheless specific measures aimed to limit the habitat erosion and invasion of exotic plants should be adopted in all European countries, especially those where urban and industrial areas are now rapidly developing after difficult political and economic historical periods (e.g. Balkan countries).

Conservation Status:
Annex 1 types:
3220: ALP U1, ATL XX, BOR FV, CON U1, MED U1
3230: ALP U2, CON U2, MED U1
3240: ALP U1, ATL U1, CON U1, MED U1

Capacity to Recover its Typical Character and Functionality?:
The capacity of this habitat to recover differs according to the type of damage that the habitat has undergone. If, as is most frequent, the damage influences the hydrology and morphology of the stream or its basin, the recovery time can be very long or even unattainable and restoration always requires intervention. If the damage is from water pollution, the habitat can be restored in a relatively short time (10 years, or even less) but anyway through intervention and the complete removal of the causes of pollution.

Summary:
This habitat type of sparsely vegetated or bare streambeds and banks has a relatively wide distribution in Europe occurring in all mountain and Boreal areas. Its biological diversity mainly depends on the particular altitudinal belt in which it develops and on the energy of the waterflow that characterize the stream but in general it is a very dynamic habitat characterized by pioneer and ephemeral plant communities, their development repeatedly interrupted by torrential flow. The main pressures on this habitat are exploitation of water energy with dam construction and barriers, and extraction of gravel and sand and the development of industrial, agriculture and urban areas. The probability of recovery when the habitat is very damaged by the construction of human infrastructure is very low without complete restoration of the original hydrological regime.

References:
Delarze, R. and Gonseth, Y. 2008. Guide des millieux naturels de Suisse. Rossolis, Bussigny.
Minelli, A., Ruffo, S. and Stoch, F. (Coord.) 2002. Quaderni Habitat. Torrenti Montani. La vita nelle acque correnti. Ministero dell’Ambiente e della Tutela del Territorio, Museo Friulano di Storia Naturale – Comune di Udine, Udine.
Gaudillat, V., Haury, J., Barbier, B. and Peschadour, F. (Coord). 2002. Cahiers d’habitats – Tome 3 – Habitats humides. La Documentation française, Paris.
Påhlsson, L. (ed.) 1994. Vegetationstyper I Norden. TemaNord 1994: 665. Nordic Council of Ministers, Copenhagen.

Criterion A Text:
The calculated trend in quantity of the habitat resulted in a reduction of 34-36% during the last 50 years that corresponds to the category Vulnerable according to criterion A1. A slightly higher historic negative trend since 1750 of 43-45% leads to assessment as Near Threatened according to criterion A3. The calculation of the recent trend was performed using the quantitative data available, which represent around 70% of the countries in which the habitat occur. Therefore this calculation can be considered quite reliable. Only 4 countries (around 30%) provided data concerning the historical trend, therefore for the calculation it was assumed the habitat is at least stable in all the other countries.

Criterion B Text:
The habitat is very extensive in Europe, therefore both EOO and AOO are far from the thresholds required by criterion B to consider the habitat threatened. However the spatial extent and the biotic and abiotic quality of the habitat are in continuing decline.

Criterion C/D Text:
The reduction in biotic and abiotic quality over the last 50 years affected 31% of the extent of the habitat countries with a severity of 33% both in EU28 and EU28+. This calculation is based on data by around 60% of the countries in which the habitat is expected to occur. According to criterion C/D the habitat is Least Concern.

Synthesis:
This habitat type is relatively wide distributed in Europe but, during the last centuries, it has undergone a relatively high reduction in quantity (34-36% in the last 50 years) due to the rapidly increasing urbanization and development of agriculture and industrial activities after the Second World War. The habitat is therefore assessed as Vulnerable according to criterion A1.

Sub-habitats in Need of Examination:
Further investigations about this habitat are necessary in the Balkan countries within EU28+.

Contributors:
Type description: G. Arts, F. Landucci, J.A. Molina, B. Poulin, H. Toivonen, V. Kalníková
R. Delarze, P. Ivanov, J. Šibík, D. Paternoster, A. Ssymank, P. Finck, U. Raths, U. Riecken, E. Agrillo, S. Armiraglio, S. Assini, F. Attorre, G. Buffa, L. Casella, D. Gigante, G. Pezzi, D. Viciani, A. Mikolajczak, A. ÄŒarni, N. Juvan, T. Kontula, C. Bita-Nicolae, J.A. Molina, Ä. MilanoviÄ‡
Working Group Freshater:, G. Arts, F. Landucci, J.A. Molina, B. Poulin, H. Toivonen


Habitat Description:
Communities generally dominated by tall sedges typically of the order Magnocaricetalia. Cladium mariscus communities are only partly included here. When they develop in calcareous fens they are part of the habitat type D4.1c. The optimal belt for tall sedge vegetation is the geolittoral zone, the area above the mean water level, but subjected to periodical flooding and water saturated for most of the year. Tall sedge communities are usually species-poor, often dominated by one species and accompanied by few characteristic species. Some of the above mentioned dominant species have clear preferences related to climate, substrate, hydrology and trophic level of the habitat.  The primary productivity of these communities is high, but clearly lower than for non-sedges tall helophytes included in the habitat C5.1a.
Tall sedge communities occur also along running waters or in wet and moist depressions of alluvial and karst plains. In the hydro-series they are later replaced by drier wet meadows and riparian shrub vegetation. They grow as fringe vegetation along lakes and ponds, often in mixture with tall reedy helophytes and forbs (habitat C5.1a). In low-productive lakes, particularly in northern Europe, Carex rostrata, C. lasiocarpa and C. aquatilis, with Equisetum fluviatile, are substituting taller reeds in water fringe helophyte vegetation. Such stands are very species poor, sometimes monospecific. However stands dominated by Carex rostrata and C. lasiocarpa in calcareous fens and bogs belong to the habitats D4.1c
Many tall sedges have an effective clonal growth: some species grow in large tussocks raising some tens of centimetres above the substrate. Wet hollows between tussocks, with accumulation of plant remains, are often occupied by small aquatic and emergent herbs and grasses (e.g. Galium palustris s.l., Lycopus europaeus, Ranunculus trichophyllus, Scutellaria galericulata, Lemna spp., Utricularia ssp.), aquatic mosses and hepatics (Calliergon spp., Drepanocladus aduncus, Riccia spp., Ricciocarpos natans). Various mixtures of herbs and grasses often indicate unstable successive states after disturbances.
Tall sedge communities have been earlier used for cattle grazing and mowing, and many have been converted to arable land and pasture. They are largely impacted by water level regulation, construction activities and eutrophication. In recent past eutrophication and decline of grazing has often led to the increase of tall reeds in the lower part of tall sedge communities, and to increase of shrubs and trees in the upper part. Tall plants from drier positions can also invade sedge-dominated stands. In dynamic alluvial landscapes this habitat may exist more sustainable, occupying slightly different sites over different years. In other sites it can only be maintained for longer times by mowing.
Indicators of good quality:
Natural water and flooding regime
No alteration of substrate chemistry
Species poor stands dominated by sedges
Low cover of annuals, ruderal and/or nitrophilous species
Low anthropogenic impacts in terms of construction activities, eutrophication, drainage etc.
No enhanced biomass due to eutrophication or replacement by tall reedy vegetation
Absence of invasive alien species (e.g. Impatiens glandulifera, Bidens frondosa, Ludwigia spp., Fallopia spp., etc.)
Shrubs and trees occur in low cover and do not show increasing trends
Low cover of tall herbs from drier positions and other habitats (e.g. Calystegia sepium, Eupatorium cannabinum, Valeriana officinalis, Cirsium spp., etc.)

Characteristic species:
Vascular plants: Calamagrostis canescens, C. purpurea, Carex acuta, C. acutiformis, C. appropinquata, C. aquatilis, C. buxbaumii, Carex cespitosa, C. diandra, C. distica, C. elata, C. hispida, C. juncella,  C. lasiocarpa, C. lyngbyei (Iceland), C. melanostachya, C. paniculata, C. pseudocyperus, C. randalpina, C. riparia, C. rostrata, C. reuteriana, C. rhynchophysa, C. vesicaria, C. vulpina, Cladium mariscus, Cyperus longus, Phalaris arundinacea. Frequently accompaning species are , Lycopus europaeus, Lythrum salicaria, Mentha aquatica, Rorippa amphibia, Oenanthe aquatica, Glyceria spp., Equisetum fluviatile, Solanum dulcamara, in the Mediterranean area also some Juncus species may occur in this habitat (e.g. J. effuses and J. inflexus).
Bryophytes: Drepanocladus spp. (mainly D. aduncus), Campylium spp., Calliergon spp., in paludified stands also Sphagnum spp.
Vertebrates: Rana spp., Hyla spp., Bombina spp., Bufo spp., Natrix spp., Hierophis viridiflavus (Mediterranenan area). If this habitat is close to rivers or lakes can be important bird haunts. The species of the family Ardeidae are rather frequent.
Invertebrates: Nematoda, Lumbricus spp., Odonata, Larinioides spp., Dolomedes fimbriatus, D. plantarius, Argiope spp.

Classification:
EUNIS:
D5.2 Beds of large sedges normally without free-standing water
EuroVegChecklist (alliances):
Magnocaricion elatae Koch 1926
Magnocaricion gracilis Géhu 1961
Caricion broterianae (Rivas-Martinez et al. 1986) J.A. Molina 1966
Phalaridion arundinaceae Kopecký 1961
Caricion microcarpae Gamisans 1975
Annex 1:
6450 Northern boreal alluvial meadows
Emerald:
D5.2 Beds of large sedges normally without free-standing water
MAES-2:
Wetlands
IUCN:
5. Wetlands (inland)

Justification Outstanding Example of Biogeographical Region:
This habitat occurs in whole Europe, but different species are dominant in different ecological (substrate and nutrient) conditions.

Map Description:
Map has many data gaps, for example in Poland, Norway, the Balkan and Romania, depending on availability of data in EVA and GBIF. Data sources: EVA, GBIF, NAT.

Comment EU28+:
Only 34% of the countries provided the total area.

Trends in Quantity:
The habitat type results to have a general decreasing trend in quantity. Most countries for which data are available reported a decrease of the habitat between 10 and 80% with a resulting total reduction in Europe of 45-48% during the last 50 years. An even more serious decrease of the habitat is recorded by in the historical past (50-250 years ago). In this case the countries that were able to provide historical data indicated a decrease between 40 and 90% with a resulting total reduction in Europe between 43-48% of the total area. Despite the heavy decrease of the habitat in the historical past mainly due to increasing urbanization and drainage for other human uses, some countries especially from Central and Northern Europe stated that the habitat is currently stable or only slightly decreasing and expect for the future the habitat can remain stable under the current management and land use. The situation in the Southern countries appears rather different. The habitat is still decreasing (except for Bulgaria where the habitat is increasing due to water regulation of deeper marshes) and is expected to still decrease in the future.

Trends in Quality:
Most countries that provided data reported a moderate degradation of 10 to 80% of the habitat area with a resulting degradation of 54-55 % (EU28+ - EU28) of the habitat with a severity of 42-43% (EU28+ - EU28). The degradation state seems to not be differentiated between Southern and Northern countries and the causes of degradations are in both cases related to increasing human pressures such as water drainage, poplar plantations and changing in the management. The degradation is increasing in some areas due to the abandonment of traditional management (seasonal mowing and pasture), changing in the land use, nitrification and general induced change of soil conditions due to agriculture pollution.

% of Distribution of the Habitat Type within the EU 28:
A broader defined similar habitat type, but hosting different species occurs in the whole boreal hemisphere. The habitat type has a Euro-Asiatic distribution but the dominant species and the general species composition change from West to East. Probably 40-50% of the habitat is within EU28, the remaining percentage is distributed among EU28+ countries and those outside Europe such as Russia, Belarus, Ukraine, Georgia, Turkey, etc.

Justification of Small Range/Regression:
The geographical range of the habitat (EOO) is very wide and, despite the decrease in the last 50 years has been rather important (more than 40%), seems far to go under 50,000 Km2.

Justification of Restricted Area:
The habitat does not have intrinsically restricted area and range.

Pressures and Threats:
Main pressures during the past and present time are represented by tentative land melioration for the expansion of agriculture, industrial and urban areas. During the past centuries alluvial plains of many European countries, especially in those areas where mountain landscape prevails have been completely drained and transformed in arable lands or urban areas. Superficial and groundwater pollution especially related to agriculture is a very frequent problem. The drainage of the habitat is very often accompanied by plantation of trees for paper production such as Populus spp. and Robinia pseudoacacia. Despite the human land erosion has been limited in this habitat during the last years in several countries, one future threat is represented by climate changes that could result in a change of the hydrological regime.

Conservation and Management:
Legal measures for limiting erosion of the habitat due to expanding human activities have already been taken from some European countries during the last years. However such measures are not evenly adopted in Europe. In some countries this habitat is considered protected, in some other is not. Water abstraction and regulation are limited and regulated only when the habitat belongs to a protected area. Common regulation about land use, water abstraction and agriculture should be applied in those countries where the habitat is less frequent and abundant. Periodic grazing and mowing could have positive results for the maintenance of some vegetation types typical of this habitat and for limiting the vegetation succession processes. Traditional landscape management could be reintroduced in some areas to improve the quality of the habitat. Another useful measure may be the respect of buffer zones between the habitat and the agricultural lands. Restoring the habitat could be useful in some areas where the habitat strongly declined, however the restoration of such habitat is always very hard and often not successful.

Capacity to Recover its Typical Character and Functionality?:
The capacity of this habitat to naturally recover is different according to the kind of damage that the habitat has undergone. If the damage interested the groundwater level it may be possible to recover the habitat through hydrologic intervention and only if the chemical and physical soil conditions remained unaltered. If the damage concerns the land use, i.e. transformation of the habitat in agricultural land, trees plantation, it becomes almost impossible to properly recover the habitat due to the deep changes of the soil conditions. It could be possible through intervention recreating functionally similar conditions, but it would be difficult to have again the same species composition. There are not sufficient studies about restoration of this habitat type to have a clear vision of the efforts needed.

Summary:
This habitat develops throughout the European lowlands, though less commonly to the warmer south, on the margins of standing and slow-moving fresh waters just above the mean water level, but subject to periodic flooding and on ground that is water saturated for most of the year. Tall sedge communities are usually species-poor, often dominated by one productive plant, often of densely tussock habit, and accompanied by few characteristic species, often disposed in mosaics on and between the tussocks. The particular dominant depends on climate, substrate, hydrology and trophic level of the habitat and, now usually in the past, on management by grazing or cutting. The main threats are expansion of agricultural, industrial and urban areas and changes in the level of and pollution in the groundwater. Often the habitat is totally transformed without possibility of natural recovery and strong intervention is usually needed for recovery.

References:
Dierssen, K. 1996. Vegetation Nordeuropas. Verlag Eugen Ulmer, Stuttgart. 838 pp.
Landucci, F., Gigante, D., Venanzoni, R. and Chytrý, M. 2013. Wetland vegetation of the class Phragmito-Magno-Caricetea in central Italy. Phytocoenologia 43: 67–100.
ChytryÌ, M. (ed.) 2011. Vegetace ÄŒeské republiky 3. Vodní a mokÅ™adní vegetace. [Vegetation of the Czech Republic 3. Aquatic and wetland vegetation]. Academia, Praha, CZ.

Criterion A Text:
The calculated trend in quantity resulted in a reduction of 45-48% during the last 50 years that corresponds to the category Vulnerable for both EU28 and EU28+. This calculation was performed using the quantitative data available, which however represent only 50% of the total countries in which the habitat occur or is expected to occur. The trend in quantity is very close to the threshold of category Endangered. If we consider the extended lack of data the habitat could also be in this last category. However there is not sufficient information available to make such assumption. Similar is the historical trend, showing a reduction of the habitat between 43 and 48% for the last 250 years. Only 3 countries provided data concerning the historical trend and therefore this is insufficent for an assessment. However the habitat probably decreased throughout most of the other European countries.

Criterion C/D Text:
The reduction in biotic and abiotic quality over the last 50 years affected 54-55% of the extent of the habitat in Europe with a severity of 42-43%. This calculation is based on data provided by approximately 50% of the countries in which the habitat is expected to occur. According to criterion C/D the habitat is Near Threatened. A similar trend in quality is expected in the countries for which there are no data, however a slight underestimation or overestimation may be due to the rather large gap of data. In case of slight underestimation of severity the habitat would result Vulnerable.

Synthesis:
This habitat type still has a wide distribution in Europe, despite a very large reduction in quantity (45-48%) and quality (relative severity of 42-43% on 54-55% of the extent) during the last 50 years, mainly due to intensification of agricultural land use. The habitat reaches the thresholds of Vulnerable (VU) for both EU28 and EU28+ according to criterion A1, and the figures are close th the Endangered threshold. According to criterion A3 and C/D1 the habitat qualifies for Near Threatened (NT), and in both cases values are very close to the threshold of Vulnerable. The assessment was carried out using data from only about 50% of the countries in which the habitat occur. Despite this, according to expert knowledge and literature, there is no argument to assume a very different situation in the rest of Europe.

Sub-habitats in Need of Examination:
This habitat type has a wide distribution, however is surely more threatened in the drier parts of Europe, such as the Southern European countries and particularly the Mediterranean region. The habitat is in these areas very often restricted to the mou

Contributors:
Type description: H. Toivonen, F. Landucci, G. Arts, J.A. Molina, B. Poulin.
Territorial data: R. Tzonev, Zs. Molnár, J.Capelo, D. Espírito-Santo, K. Šumberová, D. Paternoster, R.Delarze, A. Ssymank, P. Finck, U. Raths, U. Riecken, E. Agrillo, S. Armiraglio, S. Assini, F. Attorre, G. Buffa, L. Casella, D. Gigante, G. Pezzi, R. Venanzoni, D. Viciani, A. Mikolajczak, J. Brophy, J. Šibík, L.M. Delescaille, V. RašomaviÄius, A. ÄŒarni, N. Juvan, E. Weeda, T. Kontula, Å½. Škvorc, C. Bita-Nicolae, J.A.Molina, Ä. MilanoviÄ‡, J. Rodwell
Working Group Freshwater Habitats: G. Arts, F. Landucci, J.A. Molina, B. Poulin, H. Toivonen


Habitat Type Name:
A5.28: Faunal communities of sheltered Mediterranean infralittoral muddy sands

Habitat Description:
This habitat is situated in sheltered environments, such as embayments, with low hydrodynamic regime, and thus in stable sedimentary systems, at depths between 1-15 m. The substrate consists of a muddy-sandy sediment where the sand fraction is usually composed by mollusc shells. Organic matter and silt-clay contents are the primary driving factors determining species composition. The very variable environmental conditions of these shallow environments in terms of salinity and water temperature determine that these habitats are colonized by euryhaline and eurytherm organisms.
This habitat can be naturally colonized by seaweeds or seagrasses. When seaweeds and seagrasses are absent, polychaetes dominate the invertebrate assemblages, mainly Neanthes caudata, Pseudomastus deltaicus, Notomastus latericeus, Ampharete finmarchica, Mediomastus fragilis, Aonides oxycephala and Heteromastus filiformis together with some crustaceans (Ampelisca brevicornis and Leucothoe incisa). The phoronid Phoronis psammophila is also very abundant. The bivalves Thracia papyracea and Cerastoderma glaucum dominate amongst filter-feeding invertebrates although the presence of Loripes lacteus is also frequent. Holothurians and gastropods Cyclope neritea and Nassarius reticulatus are common deposit-feeders, sliding on the substrate. The presence of sensitive species such as the mollusc Pinna nobilis is not very frequent but it can be occasionally observed. The eel Anguilla anguilla, the Sea Bass Dicentrarchus labrax, the gobids Gobius spp. and soles (Solea spp.) are amongst the most common fishes. When macroalgal species are present, Acetabularia calyculus, Ulva spp. and Cladophora spp. are the most abundant. The main seagrasses are Zostera noltii and Cymodocea nodosa.
Five different sub-habitats have been described for muddy sands habitat, with different dominant species and under slightly different conditions. These are the sub-habitat with Caulerpa prolifera on sheltered superficial muddy sands; and the sub-habitat with Pestarella (=Callianassa) thyrrena and Kellia sp. where the silt-clay fraction is >5% and the organic matter content reaches moderate to high values. There is a sub-habitat associated to freshwater discharge with Cerastoderma glaucum and Cyathura carinata in compact sediments which is characteristic of organically polluted environments in brackish waters; aub-habitat with Loripes lacteus and Ruditapes species in muddy sands on bays, estuaries, coastal lagoons and other sheltered environments, always at shallow zones that are highly influenced by seawater; and a sub-habitat of hydrothermal oozes with Cyclope neritea and nematodes which is only present in shallow waters (< 10m) with high sulfide concentrations, high sediment temperatures and high salinities. 
Indicators of quality:                                                                                                                   
Most of the species included in the habitat description are bioindicators of environmental quality. The majority of bivalves are very sensitive to eutrophication, and more tolerant and opportunistic species tend to dominate with increasing eutrophication. Changes in abundance and richness of fauna composition are good indicators of trends in habitat quality. Ruditapes decussatus has been proposed as a pollution bioindicator in areas where mussels are not available. The accumulation of pollutants in Ruditapes’ tissues has been used to assess environmental quality.
Characteristic species:
Characteristic species include molluscs: Cerastoderma glaucum, Thracia papyracea, Loripes lacteus, Cyclope neritea, Nassarius reticulatus, Pinna nobilis, Kellia sp., Scrobicularia plana, Abra spp., Ruditapes decussatus, Ruditapes philippinarum, Lentidium mediterraneum, Tellina tenuis, Venerupis aureus. 
Crustacea: Ampelisca breviconis, Leucothoe incisa, Pestarella thyrrena, Corophium spp., Cyathura carinata, Psudolirius kroyeri, Idotea baltica, Iphinoe inermis, Upogebia pusilla. 
Seagrasses: Zostera noltei, Cymodocea nodosa; phoronidea: Phoronis psammophila; nematoda: Oncholaimus campylocercoides, annelida: Neanthes caudata, Pseudomastus deltaicus, Notomastus latericeus, Ampharete finmarchica, Heteromastus filiformis, Nephthys spp., Streblospio shrubsolii, Nereis diversicolor, Cirrophorus furcatus, Platynereis dumerilii, Capitella capitata, Mediomastus fragilis, Harmothoe spinifera, Abarenicola claparedii, Chone collaris, Petaloproctus terricolaâ€‹; 
Chlorophyta (green algae): Caulerpa prolifera, Acetabularia calyculus, Ulva spp., Cladophora spp. 
and fish species such as: Anguilla anguilla, Dicentrarchus labrax, Gobius spp., Solea spp.

Classification:
EUNIS (v1405):
Level 4: A sub-habitat of 'Mediterranean sublittoral sands' (A5.2)
 
Annex 1:
1130 Estuaries
1160 Large shallow inlets and bays
 
MAES:
Marine – Coastal: Shallow Sublittoral Sediment
 
MSFD:
Shallow Sublittoral sands
 
EUSeaMap:
Infralittoral sands
 
IUCN:
9.5. Subtidal sandy mud
9.10. Estuaries

Map Description:
There are insufficient data to provide a comprehensive and accurate map of the distribution of this habitat. This map has been generated using EMODnet data from modelled/surveyed records from the Mediterranean (and supplemented with expert opinion where applicable) (EMODnet, 2015). EOO and AOO have been calculated on the available data presented in this map however these should be treated with caution as expert opinion is that this is not the full distribution of the habitat.

Trends in Quantity:
There are very few reports that describe trends of this habitat in the Mediterranean Sea, and most of the scientific studies have focused on the descriptions of the communities or the ecological characteristics of some particular species at few sites. Episodes of Caulerpa prolifera proliferation have been reported in the western Mediterranean during the 1920s and within the Levantine basin during much of the first half of the 20th century. In several cases, the meadows produced by Caulerpa proliferated rapidly and then, for reasons that are not well understood, disappeared or declined appreciably in abundance. The information regarding trends on other sub-habitats is unavailable.
Given that most of this habitat is dominated by different opportunistic species that can stand or thrive under moderate to high organic loads, it is suggested that the habitat could be considered stable in the EU 28 but over all the trend is unknown. Its average current trend in quantity in the EU 28+ remains unknown.

Trends in Quality:
Most of the species included in the habitat description are bioindicators of environmental quality. The concentration of heavy metals and other pollutants found in the soft tissues of some species such as Cerastoderma glaucum or Ruditapes decussatus in Mediterranean shallow environments such as Ethang de Thau lagoon in France, Izmir Bay in Turkey or Mar Menor in Spain may indicate an overall tendency of decrease in the quality of the habitat. However, there is not enough information at present to determine trends in quality for this habitat.

% of Distribution of the Habitat Type within the EU 28:
Limited information regarding this habitat is available and much of its current distribution in the eastern Mediterranean is unknown or unavailable. Therefore, it is not possible to estimate how much of its current distribution lies within the EU 28.

Justification of Small Range/Regression:
The habitat has a natural range >50,000 km2.

Pressures and Threats:
Pressures to sheltered infralittoral muddy sands communities include mainly pollution, eutrophication and bottom trawling. The species present in this habitat are very sensitive to eutrophication, and more tolerant and opportunistic species tend to dominate with increasing eutrophication. Other coastal human activities such as dumping or discharge of solid or liquid wastes at sea, dredged sediment disposal, untreated discharge and effluents from industrial plants, agriculture, aquaculture farms and building activities can affect directly or indirectly this habitat type.
Direct mechanical damage and habitat modification caused by construction of ports and marinas together with benthic fishing activities such as bivalve mollusc exploitation, particularly bottom-towed fishing gear, and beach seining are also important. This can cause physical disturbance and a decline in species richness.

Conservation and Management:
There are no specific conservation actions currently in place for this habitat. The broad distribution of this habitat makes it likely that it occurs in protected areas, however detailed information is missing. A wide survey to assess the distribution of this habitat is needed in order to better evaluate its conservation and management. The designation of reference sites for long monitoring trends and the continuation of those monitoring schemes already in place will assist to examine the trends in this habitat.
Improving spatial and strategic planning of human activities, in particular to promote the wiser use of habitats where there are competing demands (e.g. fishing), and the reduction of coastal pollution and eutrophication and improvement of water quality are necessary to ensure the good conservation status of this habitat in the Mediterranean.

Conservation Status:
Annex 1:
1130 MMED U2
1160 MMED XX
Listed as endangered natural habitat type in the Resolution no. 4 (1996): Sublittoral soft seabeds (code 11.22).
Under the Barcelona Convention, species such as the mollusc Pinna

Summary:
This habitat typically develops at closed or semi-closed brackish water lagoons, estuaries and sheltered bays on sandy and muddy bottoms of the upper sublittoral zone. It is widely distributed through the Mediterranean although its geographical distribution in the eastern Mediterranean is less known. The habitat is characterised by the dominance of different species, mostly opportunistic fauna and flora that is able to stand moderate to high organic loads from coastal areas. 
Threats from a variety of human activities, particularly from construction and discharges but also associated changes in local water flow/chemistry and benthic dredging and fishing, are directly linked to some of the impacts observed on this habitat type. A decrease on the quality of the habitat due to industrial pollution has been reported at different environments accross the Mediterranean Sea. Nevertheless, the impact on the communities of this habitat needs to be further studied as relatively little is known about its ecology and trends.There are no specific conservation actions currently in place for this habitat. A wide survey to assess the distribution of this habitat is needed in order to better evaluate its conservation and management. The designation of reference sites for long monitoring trends and the continuation of those monitoring schemes already in place will assist to examine the trends in this habitat. Improving spatial and strategic planning of human activities, in particular to promote the wiser use of habitats where there are competing demands (e.g. fishing) and the reduction of coastal pollution and eutrophication and improvement of water quality are necessary to ensure the good conservation status of this habitat in the Mediterranean.

References:
Akoumianaki, I. and Nicolaidou, A. 2007. Spatial variability and dynamics of macrobenthos in a Mediterranean delta front area: The role of physical processes. Journal of Sea Research 57: 47-64.
Egemen, O., Sunlu, U. and KaymakçÄ±, A. 1998. Heavy metal concentrations in some molluscs and in surficial sediments from Izmir Bay/Turkey. 35th CÄ°ESM Congress Proceedings, Dubrovnik (Croatie) 35 (1), 250-251.
Doumenge, F. 1995. Quelques re´flexions sur les algues Caulerpes. Biol. Mar. Mediterr. 2: 613–633.
Giménez, F. and Marín, A. 1991. Los anélidos poliquetos de una solfatara submarina en el Golfo de Nápoles. Anales de Biología 17: 143-151.
HCMR (Hellenic Centre for Marine Research), 2012-2015. The monitoring network for the ecological status quality of the transitional and coastal waters of Greece according to article 8 of the WFD 2000/60/EC. HCMR-MINENV. Edited by N. Simboura and P. Panayotidis. Technical Report, (In Greek). 
Jordana, E., Pinedo, S. and Ballesteros, E. 2015. Macrobenthic assemblages, sediment characteristics and heavy metal concentrations in soft-bottom Ebre Delta bays (NW Mediterranean). Environmental Monitoring and Assessment 187: 71.
Jaubert, J.M., Chisholm, J.R.M., Minghelli-Roman, A., Marchioretti, M., Morrow, J.H. and Ripley, H.T. (2003). Re-evaluation of the extent of Caulerpa taxifolia development in the northern Mediterranean using airborne spectrographic sensing. Marine Ecology Progress Series, 263:75–82.
Massé, H. 1972. Quantitative investigations of sand-bottom macrofauna along the Mediterranean north-west coast. Marine Biology 15: 209-220.
Ladhar-Chaabouni, R., Macherki-Ajimi, M. and Hamza-Chaffai, A. Spatial distribution of cadmium and some biomarkers in Cerastoderma glaucum living in a polluted area. Marine Biol Res 2009; 5: 478-86. http://dx.doi.org/10.1080/
Ollivier, G. 1929. Etude de la flore marine de la Coˆte d’Azur. Ann. Inst. oce´anogr., Paris 8, No 3.
Rayss, T. 1941. Sur les Caulerpes de la coˆte palestinienne. Palest. J. Bot. Jerusalem 2: 103–124.
Relini, G. and Giaccone, G. (Eds), 2009. Priority habitats according to the SPA/BIO protocol (Barcelona Convention) present in Italy: Identification sheets. Biol. Mar. Mediterr. 16 (Suppl.) 200-203.
Sánchez Moyano, J.E., García Adiego, E.M., Estacio, F.J. and García Gómez, J.C. 2001. Influencia de la densidad de Caulerpa prolifera (chlorophyta) sobre la composición de la macrofauna en una pradera en la bahía de Algeciras (sur de España) Ciencias Marinas, vol. 27, núm. 1,  pp. 47-71 Universidad Autónoma de Baja California Ensenada, México.
Sardá, R., Martin, D., Pinedo, S., Dueso, A. and Cardell, M.J. 1996. Seasonal dynamics of shallow soft-bottom communities in western Mediterranean. In: "The Biology and Ecology of shallow-coastal waters" (D. Eleftherion, ed.). Olssen & Olssen Publications. pp. 191-198. Proceedings of the 28th EMBS.
Tlig-Zouari, S. and Maamouri-Mokhtar, F. 2008. Macrozoobenthic species composition and distribution in the Northern lagoon of Tunis. Transitional Waters Bulletin TWB, Transit. Waters Bull. 2, 1-15.
Sanchiz, C., García-Carrascosa, A.M. and Pastor, A. 2005. Bioaccumulation of Hg, Cd, Pb and Zn in Four Marine Phanerogams and the Alga Caulerpa prolifera (Försskal) Lamouroux from the East Coast of Spain. Botanica Marina 42(2): 157–164, ISSN (Print) 0006-8055.
Szefer, P., Wolowicz, M., Kusak, A., Deslous Paoli, J.-M., Czarnowski, W., Frelek, K. and Belzunce, M.J. 1999. Distribution of mercury and other trace metals in the cockle Cerastoderma glaucum from the Mediterranean Lagoon Etang de Thau. Arch. Environ. Contam. Toxicol. 36(1): 56-63
Simboura, N. and Zenetos, A. 2002. Benthic indicators to use in Ecological Quality classification of Mediterranean soft bottom marine ecosystems, including a new Biotic Index. Mediterranean Marine Science, Vol. 3/2, 77-111.
Simboura, N. and Nicolaidou, A. 2001. The Polychaetes (Annelida, Polychaeta) of Greece: checklist, distribution and ecological characteristics. Monographs on Marine Sciences, Series no 4. NCMR.
Simboura, Ν., Katsiaras, Ν., Diliberto, S., Naletaki, M., Plaiti, W. and Arvanitakis, G. 2015. Benthic communities of the National Monitoring Network for the ecological quality of the Greek coastal waters. Proceedings 11th Hellenic Symposium of Oceanography & Fisheries. 13-17 May 2015, Mytilini, Lesvos, 685-688.
Simboura, N., Kyriakidou, Ch., Drakopoulou, P. Salomidi, M. and Sakellariou, D. 2015. A methodological approach for mapping the soft bottom zoobenthic habitats of Greece. Proceedings 11th Hellenic Symposium of Oceanography & Fisheries. 13-17 May 2015, Mytilini, Lesvos, 501-504.
Thiermann, F., Akoumianaki, I., Hughes, J.A. and Giere, O. 1997. Benthic fauna of a shallow-water gaseohydrothermal vent area in the Aegean Sea. Marine Biology 128: 149-159.
Voultsiadou E., Koutsoubas, D. and Achparaki, M. 2010. Bivalve Mollusc Exploitation in Mediterranean Coastal Communities: an historical approach. Journal of Biological Research. 12: 1-12.

Criterion A Text:
There is insufficient information regarding the historical, present or future reduction of this habitat in the Mediterranean Sea, and there are no country monitoring programs in place to examine past and future trends. Therefore, the habitat type is assessed as Data Deficient under Criterion A.

Criterion B Text:
This habitat has a large natural range in the Mediterranean region. The precise extent is unknown however as EOO >50,000km2 and AOO >50, this exceeds the thresholds for a threatened category on the basis of restricted geographic distribution. Trends in quality and quantity are unknown. The distribution of the habitat is such that the identified threats are unlikely to affect all localities at once. This habitat has therefore been assessed as Least Concern under criteria B1(c) B2 (c) and B3 and Data Deficient for all other criteria.

Criterion C/D Text:
The assessment of reduction in abiotic and/or biotic quality is difficult due to the lack of studies and data on past and present state conditions. Nonetheless, slight changes have been reported in the abiotic conditions (increase of heavy metals and eutrophication) of this habitat across its eastern and western Mediterranean distribution over last 50 years. However, the extent of this decline is unknown. Therefore, the habitat type is assessed as Data Deficient under Criterion C/D1.

Synthesis:
This is a relatively poorly studied habitat type and limited information exists regarding its distribution and habitat quantity across the Mediterranean Sea. Its wide distribution combined with the dominance by certain opportunistic and tolerant species, despite a slight decrease on habitat quality, seems to indicate the habitat could qualify for Least Concern under Criterion B. However given that the habitat has not been studied in enough detail in the past and that the territorial data does not provide information for most Mediterranean countries, the assessment of this habitat is assessed Data Deficient for both EU 28 and EU 28+


Habitat Type Name:
H4.3 Rock glacier and unvegetated ice-dominated moraine

Habitat Description:
As indicated by its name, a rock glacier is a mixture of frozen rock detritus and ice. It takes the form of a lobate, spatulate or tongue-like mass of angular boulders, behaving as a lava flow, due to the presence of internal ice that flows very slowly under gravity forces. This movement is 100 to 1000 times slower than in a true glacier. The origin of ice of rock glaciers can be glacial or periglacial; thereby, rock glacier occurs also when permafrost (frozen soil) creeps downslope during thaw periods. This habitat type is endangered by the global warming of the climate. Moraines are glacially formed accumulations of unconsolidated mineral debris. Ice-dominated moraines occur in the vicinity of retreating glaciers. Few organisms have the ability to colonize these particular habitats, because of the low temperatures and the mobility of the substrate. The flora is limited to pioneer plants, lichens and some vascular plants, occurring principally on the lateral and terminal borders of the rock glacier. Active rock glaciers have a very low vegetation cover, while inactive or relict ones are characterized by higher covers (>70%). The diversity of the fauna increases with the vegetation cover; it includes Collembola, spiders, Homoptera, Diptera, parasitoid wasps, ground beetles and aphids. These ice-rich formations are found in altitude or in high latitudes. In Europe, they occur only in the high mountain regions of the Alps, the Pyrenees, the Scandes, and in the arctic region. 
Indicators of good quality:
Independently of the poverty of the flora and fauna of this habitat, quality can be estimated by the degree of activity of the rock glacier. An active rock glacier moves because it has ice-rich frozen debris and its internal temperature is low. Inactive and fossil rock glaciers haven’t coherent ice-core and stop moving. 
Characteristic species:
Algae: Chlamydomonas nivalis
Lichens: Cetraria islandica, Rhizocarpon geographicum
Vascular plants: Androsace alpina, Arabis alpina, A. caerulea, Artemisia mutellina, Cardamine resedifolia, Cerastium uniflorum, Erigeron uniflorus, Gentiana bavarica, Geum reptans, Leucanthermopsis alpina, Linaria alpina, Oxyria digyna, Poa alpina, P. laxa, Prizelago alpina, Ranunculus glacialis, Salix herbacea, S. retusa, Saxifraga, bryoides, S. exarata, S. oppositifolia, S. seguieri, Sibbaldia procumbens
Fauna: Collembola, Homoptera

Classification:
EUNIS:
H4.3 Rock glaciers and unvegetated ice-dominated moraines
Annex 1:
8340 Permanent glaciers. This Annex 1 habitat type applies to a geographically and altitudinally wider range of snow or ice-dominated habitats. H4.3 is therefore narrower circumscribed than 8340.
Emerald:
H4.3 Rock glaciers and unvegetated ice-dominated moraines
MAES-2:
Sparsely vegetated land
IUCN:
6. Rocky areas

Justification Outstanding Example of Biogeographical Region:
The habitat occurs at highest altitudes of Alpine region and arctic part of Boreal biogeographical region under specific climate and geomorphological conditions.

Map Description:
No data is available. The distribution of glaciers is given as the potential distribution. Data: Art17, BOHN.

Trends in Quantity:
The total area has not been calculated. For example true glaciers in Norway are currently retreating and the expected development of climate means that the area of rock glaciers and moraines occupied by that habitat will increase (it makes up more than 10% of the area of true glaciers for the past 200 years) . In the Alps and Pyrenees, this process is much more dynamic. Nevertheless, there are some discrepancy, e.g. between small area in Spain and relatively large in Greece, (Hughes et al. 2003), which could be induced by an unclear understanding of the habitat H4.3 at all. Expected occurrence is also in remainder Alpine countries, such as Slovenia, Germany, and probably also in Bulgaria. Important missing data are from Sweden, Iceland, Norway and other arctic regions.

Trends in Quality:
Missing data. In accordance to the climate change there are also prerequisites in decreasing of the quality.

% of Distribution of the Habitat Type within the EU 28:
Distribution in countries (EU28+): AT, CH, DE, ES, FI, FR, GR, IS, IT, NO, PL, RO, SE, SK, SL, SW Outside the Europe 28+ the type is found in Greenland, Russia (Caucasus Mts).

Justification of Restricted Area:
In some regions represent the rock glaciers a small relict islands of post glacial time (Pleistocene), partly they are also periglacial forms, such as small glaciers covered by debris and rocks (Hughes et al. 2003).

Pressures and Threats:
The rock glaciers represent a fragile habitat, which can be under stress as a result of human and environmental activities. Increased leisure, mobility, wealth, easier accessibility of the mountains in Europe (a greater use of the ski areas) induce changes more than ever before. The pressure of human activities, as well as the effects of climate change and global warming on the glaciers will inevitably affect the environment and call for needs to utilise sustainable development strategies in order to control the impact on its environment. 
The main pressures are: 1/ climate change and global warming, incl. less snowfall. 2/  raising the temperature due dark rocks covering the ice mass below and absorbing heat. 3/ Mountaineering, tourism, skiing and other leisure activities in mountains. 4/ Acid rains and air pollution.

Conservation and Management:
Management and conservation of rock glaciers is not practically possible, only small threats can be reduced (direct human impact by tourism, leisure activities in mountains, local air pollution etc.

Conservation Status:
Annex 1 type:
8340: ALP U1, BOR U1
(This Annex 1 habitat type applies to a geographically and altitudinally wider range of snow or ice-dominated habitats. H4.3 is therefore narrower circumscribed than 8340. The overall conservation sta

Capacity to Recover its Typical Character and Functionality?:
In situation when true glaciers are currently retreating and the expected development of climate (rising temperatures) will continue, the habitat such as rock glaciers and moraines will increase in the localities on northern latitudes or higher altitudes. On the other hand, the rock glaciers and debris with interstitial ice on southern occurrence (Balkan countries, Spain) could disappear at all.

Summary:
These are habitats found in extreme cold at high latitudes and altitudes in Europe. A rock glacier is a mixture of frozen rock detritus and ice of glacial or periglacial origin, forming a tongue-like mass which can flow very slowly under gravity. Ice-dominated moraines are masses of unconsolidated mineral debris found in the vicinity of retreating glaciers. Few organisms have the ability to colonize these particular habitats, because of the low temperatures and the mobility of the substrate so the flora is limited to pioneer plants and lichens, occurring principally on the lateral and terminal borders of the detritus.  Invertebrates increase with the developing vegetation cover. The rock glaciers represent a fragile habitat, which can be under stress as a result of tourist and rectraeional activities, also susceptible to air pollution and climate warming.

References:
References
Bischoff, Y. 2007. Diversité et mobilité des algues de neige dans les Alpes suisses. Thèse de doctorat , Université de Genève, no. Sc. 3914, Suisse.
Barsch, D. 1996. Rock-glaciers: indicators of the present and former geoecology in high mountain environments. Springer Verlag, Berlin. 331 p.
Conardin, A., Frauenfelder, R., Ruffet, J., Hoelzle, M. and Kääb, A. 2004. Vegetation on Alpine rock glaciers surfaces: a contribution to abundance and dynamics on extreme plant habitats. Flora 199: 505-515.
DobiÅ„ski, W., Grabiec, M. and Gadek, B. 2011. Spatial relationship in interaction between glacier and permafrost in different mountainous environments of high and mid latitudes, based on GPR research. Geological Quaterly 55(4): 375-388.
Hughes, P.D., Gibbard, P.L. and Woodward, J.C. 2003. Relict rock glaciers as indicator of Mediterranean paleoclimate during the Last Glacial Maximum (Late Wurmian) in northwest Greece. Journal of Quaternary Science 18(5): 431-440.
Krainer, K. and Ribis, M. 2012. A Rock Glacier Inventory of the Tyrolean Alps (Austria). Austrian Journal of Earth Sciences 105(2): 32-47.
Lambiel, C. ( 2006). Le Pergélisol dans les terrains sédimentaires à forte déclivité: distribution, régime thermique et instabilités. Thèse de doctorat, Université de Lausanne, Suisse.
Rubin, J., Balatka, B. et al. 1986. Atlas skalních, zemních a pudních tvaru. Academia, Praha. 385 p.

Criterion A Text:
The average trend has been based on data from only three countries (France, Austria, Switzerland), but these are the countries which reported the largest areas. Important data gaps exist for the boreal countries (Sweden, Norway, Iceland), and additional data from these countries might reduce the negative trend. On long term trends only data from France and Switzerland are available, not allowing a reliable analysis.

Criterion B Text:
Although exact distribution data is missing (calculated AOO and EOO are a rough estimate based on occurrence of glaciers), it is likely that the range extent is wide (from Scandinavia to the Alps). Within the EU28 the AOO is however likely to be restricted, slightly above or below 50. Exact data are unknown, and a conservative Near Threatened status is given for criterion B2 for the EU28. Other criteria under B are assessed as Least Concern.

Criterion C/D Text:
The calculation of trends in quality is based on data from Austria and France only. However, similar trends can be expected for Switzerland, and therefore the same figures are given for the EU28+. Again, important data gaps exist for boreal countries, which may cause an overstimation of threat level. The average figures lead to the conclusion Near Threatened for both EU28 and EU28+.

Synthesis:
There is few information on trends and especially from boreal countries (Norway, Iceland, Sweden) data is lacking. The assessment therefore is based on data from the Alps only (France, Switzerland, Austria), giving it a low reliability. Trend data showed a bit less than 30% declines in area over the last 50 years for the EU28 (leading to the Near Threatened category), and smaller declines for the EU28+. Trends in quality over the same time period lead to a Near Threatened (NT) status for both EU28 and EU28+, while a likely small distribution (AOO, criterion B2) resulted in the same category for the EU28.

Contributors:
Type description: R. Delarze
Territorial data: E. Agrillo, S. Armiraglio, S. Assini, F. Attorre, C. Bita-Nicolae, R. Delarze,  J. Loidi, A. Mikolajczak, D. Paternoster, M. ValachoviÄ
Working Group Sparsely Vegetated Habitats: F. Essl, G. Giusso Del Galdo, A. Mikolajczak, D. Paternoster, M. ValachoviÄ, M. Valderrabano


Habitat Type Name:
A3.1x Photophilic communities without canopy-forming algae in Mediterranean infralittoral and upper circalittoral rock

Habitat Description:
This habitat is present from the upper infralittoral zone to the upper circalittoral zone. Assemblages are always algal-dominated, although some invertebrates can be common in the understory and growing as epiphytes. It consists of rocky bottoms covered by erect macroalgae that do not form canopies. The structure includes bush-forming or turf forming algae, encrusting fauna and epiphytes. The coverage of the 'bush' and turf strata is usually higher than in an assemblage dominated by canopy algae. Assemblages are also highly miniaturized (less than 20 cm high) and very rich in species (up to 110 species in a 400 cm2 area).
Species composition differs greatly depending on environmental conditions. Factors accounting for the variability on the assemblages include light availability, hydrodynamism, nutrient concentration in the seawater, substrate type, sedimentation, temperature, salinity, grazing intensity, predation, and frequency of disturbances. High densities of sea urchins (Paracentrotus lividus) can graze the algae, producing structurally less complex assemblages and even barren areas. Grazing by other fish species (Sarpa salpa or the exotic Siganus rivulatus, S. luridus) can modify the species composition. The habitat can be present both in good environmental conditions, and in rather degraded situations. 
Several associated biotopes have been described, distinguished according to the dominant species. They include; Padina pavonica and similar species growing on well-lit shallow sheltered areas subjected to a moderate grazing by sea urchins; Pterothamnion crispum and Compsothamnion thuyoides growing on shallow, shaded sheltered to moderately exposed rocks; Corallina elongata growing on shallow exposed shores; Halopteris scoparia growing on well-lit sheltered areas down to 25 meters depth, mainly on northern areas, sometimes associated to the brown algae Cladostephus spongiosus; and Codium bursa on moderately lit infralittoral rock.
Indicators of quality:
This habitat is very variable according to the degree of anthropogenic disturbance. Indicators of quality can be measured by examining trends. The first signs of decline imply substitution of species, a decrease on diversity, an increase on invasive exotic species, and an increase in opportunistic, fast-growing species like some Ulva spp., Cladophora spp., Acinetospora spp., or stress resistant like Corallina elongata or Lithophyllum incrustans. Mussels can also replace the dominant algae in shallow waters when the charge of particulate organic matter is very high.
Characteristic species:
This community is characterized by the presence of many photophilic algae covering hard bottoms. The number of species is huge, and it can be completely different according to the bathymetric level, exposure and geographical region.  
Rhodophyta (red algae)-Liagora viscida, Liagora distenta, Amphiroa rigida, Corallina elongata, Haliptilon virgatum, Tricleocarpa fragilis, Ceramium virgatum, Wrangelia penicillata, Chylocladia verticillata, Chrysymenia ventricosa, Halymenia floresii, Gelidium spinosum, Predaea ollivieri, Chondracanthus acicularis, Jania rubens, Lithophyllum incrustans, Neogoniolithon brassica-florida, Mesophyllum alternans, Halopithys incurva, Lophocladia lallemandii, Peyssonnelia squamaria, Asparagopsis armata, Asparagopsis taxiformis, Sphaerococcus coronopifolius, Laurencia obtusa, Laurencia majuscula, Digenea simplex, Rytiphlaea tinctoria, Alsidium corallinum, Pterothamnion crispum, Compsothamnion thuyoides, Plocamium cartilagineum, Schottera nicaeensis, Pterocladiella capillacea, Botryocladia botryoides, Peyssonnelia squamaria, Palisada patentiramea
Phaeophyta- Dictyota fasciola, Colpomenia sinuosa, Taonia atomaria, Dictyota cf. dichotoma, Dictyota mediterranea, Stypopodium schimperi, Lobophora variegata, Dictyota spiralis, Zonaria tournefortii, Padina pavonicoides, Padina ditristromatica, Arthrocladia villosa, Sporochnus pedunculatus, Carpomitra costata, Acinetospora crinita, Hydroclathus clathratus, Dictyota dichotoma v. intricata, Sphacelaria cirrosa,  Halopteris scoparia, Halopteris filicina, Padina pavonica, Cladostephus spongiosus, Dictyopteris polypodioides.
Chlorophyta (green algae)- Ulva rigida, Umbraulva olivascens, Dasycladus vermicularis, Flabellia petiolata, Acetabularia acetabulum, Parvocaulis parvulus, Caulerpa prolifera, Caulerpa cylindracea, Codium bursa, Anadyomene  stellata, Cladophoropsis membranacea, Cladophora prolifera. 
Porifera- Crambe crambe, Phorbas topsentii, Sarcotragus fasciculatus, Sarcotragus spinosulus, Hemimycale columella. 
Mollusca- Bittium reticulatum, Conus ventricosus, Columbella rustica, Rissoa guerinii.
Crustacea- Macropodia longirostris, Maja crispata. 
Echinodermata- Echinaster sepositus, Marthasterias glacialis, Paracentrotus lividus, Arbacia lixula, Holothuria tubulosa, Ophidiaster ophidianus, Ophiothrix fragilis. 
Fish- Labrus merula, Coris julis, Serranus cabrilla, Serranus scriba, Symphodus ocellatus, Symphodus tinca, Scorpaena porcus, Epinephelus marginatus, Sciaena umbra, Diplodus sargus, Diplodus vulgaris, Diplodus cervinus, Diplodus puntazzo, Siganus rivulatus, Parablennius pilicornis, Trypterygion delaisi, Symphodus mediterraneus, Siganus luridus, Epinephelus costae, Sarpa salpa, Chromis chromis, Mullus surmuletus, Dentex dentex, Symphodus roissali, Sparisoma cretense.

Classification:
EUNIS (v1405):
Level 4.  A sub-habitat of ‘Mediterranean infralittoral rock’ (A3.1).
Annex 1:
1160 large shallow inlets and bays
1170 Reefs
MAES:
Marine - Marine inlets and transitional waters
Marine – Coastal
MSFD:
Shallow sublittoral rock and biogenic reef
EUSeaMap:
Shallow photic rock or biogenic reef
IUCN:
9.7 Macroalgal/kelp
Barcelona Convention:
III. 6. 1. Biocenosis of infralittoral algae

Map Description:
This map has been generated using data based on EMODNet Database, IUCN and the European Environment Agency. EOO and AOO have been calculated on the available data presented in this map however these should be treated with caution as expert opinion is that this may not indicate the full distribution of the habitat.

Trends in Quantity:
No information on extent or reduction have been reported for this habitat. However, it can be expected that some reduction have taken place in relation to anthropogenic disturbances mostly in association with coastal development.

Trends in Quality:
There is little information on the quality status of this habitat. However, there could be a reduction in quality related to warming, pollution, sedimentation, invasive species and changes in grazing pressure. It has to be noted that this habitat is notably impacted by invasive algae, such as Lophocladia lallemandii and Caulerpa cylindracea, over many 'unknown' kilometers of coast line. Quality decreases are expected to continue in the future.

% of Distribution of the Habitat Type within the EU 28:
Unknown, although this habitat is present in the EU 28+.

Justification of Small Range/Regression:
This habitat has a large natural range extending throughout the Mediterranean Sea.

Justification of Restricted Area:
The extent of occurrence (EOO) exceeds 50,000 km2 therefore this habitat does not show a small natural range although it is likely that some of the associated biotopes might have a more restricted natural range.

Pressures and Threats:
Pollution, introduced species and climate change together with land use changes that produce changes in nutrients and sedimentation are the cause of loss of this habitat. Presently it is difficult to evaluate their magnitude in EU and non-EU countries because there is no rigorous historical baseline for the abundance of these habitats in the Mediterranean.

Conservation and Management:
Currently, there are no specific conservation actions in place for this habitat. Its broad distribution suggests that it occurs in protected areas, however detailed information is missing. A wide survey to assess the habitat is needed in order to better evaluate its conservation status. Thereafter, the definition of sites for monitoring the habitat quality and quantity will help to conduct an assessment and identify appropriate management measures. These are likely to include improving water quality, Marine Protected Areas (MPAs) and regulation of fisheries.

Capacity to Recover its Typical Character and Functionality?:
Unknown. Examples of successful recovery of this habitat are rare for the Mediterranean and are linked to the presence of marine protected areas (MPAs). There is also large variation in the structure of these habitats. Therefore, the time lapse for recovery will be determined according to the different stressors, communities and conditions.

Summary:
This habitat consists of rocky bottoms covered by erect macroalgae that do not form canopies. The structure includes bush-forming algae, turf forming algae, encrusting fauna and epiphytes. It is widely distributed in the Mediterranean in the shallow zone along the coastline. Predatory fishes and sea urchins can have a major role in determining the abundance of different algae and strongly modifying the ecosystem.  Pressures and threats are related to warming, invasive species, pollution, sedimentation and grazing pressure and direct anthropogenic impacts like increasing coastal development. Although it may be impacted by anthropogenic impacts, the communities are adapted to rapidly changing conditions and could be fairly resilient to such impacts. However, more efforts are needed to know its complete distribution in the Mediterranean and its conservation status and potential recovery capacity. These are likely to include improving water quality, Marine Protected Areas (MPAs) and regulation of fisheries.

References:
Ballesteros, E. 1988. Composición y estructura de la comunidad infralitoral de Corallina elongata Ellis & Solander de la Costa Brava (Mediterráneo Occidental). Investigación Pesquera 52(1): 135-151.
Ballesteros, E. 1992. Els vegetals i la zonació litoral: espècies, comunitats i factors que influeixen en la seva distribució. Arxius Secció Ciències, 101. Institut d'Estudis Catalans. Barcelona. 616 pp.
Ballesteros, E. 1993. Species composition and structure of a photophilic algal community dominated by Halopteris scoparia (L.) Sauvageau from the North-Western Mediterranean. Collectanea Botanica 22: 5-24.
Ballesteros, E. and Pinedo, S. 2004. Los bosques de algas pardas y rojas. En: A. Luque and J. Templado (eds.), Praderas y bosques marinos de Andalucía: 199-222. Consejería de Medio Ambiente. Junta de Andalucía, 350pp.
Ballesteros, E., Mariani, S., Cefalì, M.E., Terradas, M. and Chappuis, E. 2014. Manual dels hàbitats litorals a Catalunya. Generalitat de Catalunya. Departament de Territori i Sostenibilitat, Barcelona. 251 pp.
Curcó, A., Ferré, A., Font, J., Gesti, J., Vilar, L. and Ballesteros, E. 2008. Manual dels Hàbitats de Catalunya. Vol II. 1 Ambients litorals i salins. (Eds. J. Vigo, J. Carreras and A. Ferré). Departament de Medi Ambient i Habitatge. Generalitat de Catalunya. Barcelona. 312 pp.
Feldmann, J. 1937. Recherches sur la végétation marine de la Méditerranée: la côte des Albères. Revue Algologique, 10: 1-339.
Giaccone, G., Alongi, G., Pizzuto, F. and Cossu, A. 1994. La vegetazione marina bentonica fotofila del Mediterraneo: II Infralittorale e Circalittorale. Proposte di aggiornamento. Boll. Accad. Gioenia Sci. Nat. Catania, 27: 111-157.
Giaccone, G., Alongi, G., Pizzuto, F. and Cossu, A. 1994. La vegetazione marina bentonica sciafila del Mediterraneo: III Infralittorale e Circalittorale. Proposte di aggiornamento. Boll. Accad. Gioenia Sci. Nat. Catania, 27: 201-227.
Molinier, R. 1960. Étude des biocoenoses marines du Cap Corse. Vegetatio 9: 120-192.
Pérès, J.M. and Picard, J. 1964. Nouveau manuel de bionomie benthique de la Mer Méditerranée. Recueil des Travaux Statione Marine d’Endoume 31(47): 3-137.
Templado, J., Ballesteros, E., Galparsoro, I., Borja, A., Serrano, A., Marín, L. and Brito, A. 2012. Guía interpretativa: Inventario español de hábitats marinos. Inventario español de hábitats y especies marinos. Ministerio de Agricultura, Alimentación y Medio Ambiente. 229 pp.
Verges, A., Tomas, F., Cebrian, E., Ballesteros, E., Kizilkaya, Z., Dendrinos, P., Karamanlidis, A., Spiegel, D. and Sala, E. 2014. Tropical rabbitfish and the deforestation of a warming temperate sea. Journal of Ecology 102: 1518-1527.
Sala, E., Ballesteros, E., Dendrinos, P., Di Franco, A., Ferretti, F., plus other 20 Authors. 2012. The structure of Mediterranean rocky reef ecosystems across environmental and human gradients, and conservation implications. PLoS One 7(2), e32742
Kersting, D.K., Ballesteros, E., De Caralt, S. and Linares, C. 2014. Invasive macrophytes in a marine reserve (Columbretes Islands, NW Mediterranean): spread dynamics and interactions with the endemic scleractinian coral Cladocora caespitosa. Biological Invasions 16:1599-1610
OcanÌƒa, O., Ramos, A. and Templado, J. 2009. Paisajes Sumergidos de la RegioÌn de Ceuta y su Biodiversidad. 254 pp., Edita Fundación Museo del Mar de Ceuta.

Criterion A Text:
There is no quantitative information on the reduction in quantity for this habitat. Expert knowledge from different Mediterranean countries suggests that this habitat is mostly stable although some level of reduction is most probably happening due to coastal development. The habitat is therefore assessed as Data Deficient under Criterion A.

Criterion B Text:
It is estimated that both the EOO and AOO largely exceed the thresholds for a threatened category and there is no information available on whether there is a continuing decline in the spatial extent or the biotic and abiotic quality, on whether a threatening process will likely cause continuing declines in the future. Therefore, the habitat type is assessed as Data Deficient Criterion B.

Criterion C/D Text:
Based on the countries that have provided data, a slight reduction in abiotic quality has been reported for the habitat. The current trend regarding the biotic and abiotic quality of the habitat is stable to gradually decreasing. This is related to warming, pollution and sedimentation, while reduction in biotic quality is related to invasive species (invasive algae such as Lophocladia lallemandii and Caulerpa cylindracea have invaded this habitat in many sites) and changes in grazing pressure.
Both abiotic and biotic quality decreases are expected to continue in the future. Based on lack of information to calculate the reductions in abiotic and/or biotic quality, the habitat type is assessed as Data Deficient under Criterion C/D.

Criterion E Text:
There is no quantitative analysis available to estimate the probability of collapse of this habitat type, which is therefore assessed as Data Deficient under Criterion E.

Synthesis:
This is a widespread habitat in the Mediterranean Sea, however there is very little information available on its Area of Occupancy (AOO), impacts and trends in quantity and quality. Expert opinion is that the trends in quality are either stable or gradually decreasing but this cannot be quantified. Both quality and quantity decreases are expected to continue into the future.
The habitat has a large Extent of Occurrence (EOO) and AOO, and therefore it could potentially qualify as Least Concern under Criterion B but there is no information on any trends. However it has been assessed as Data Deficient for both the EU 28 and EU 28+ because of the lack of information on any trends in quantity and quality.

Contributors:
E. Ballesteros, A. GüreÅŸen, N. Eda Topçu, C. Jimenez, L. Hadjioannou and E. Alcazar.


Habitat Type Name:
A3.23 Photophilic communities dominated by calcareous, habitat-forming algae.

Habitat Description:
This habitat occurs in shallow rocky bottoms with large coverage of calcareous, habitat-forming corallines that provide a persistent biogenic structure. It develops on vertical cliffs in well exposed and illuminated conditions. Two red algae species dominate this habitat: Titanoderma trochanter and Tenarea tortuosa. Both species can occur together. Erect macroalgae grow interspersed with the corallines. They grow in places with a good water quality, a moderate to low hydrodynamism, and above 1.5 meters depth.
Indicators of quality:                                                                                                                              
There is no information on indicators of quality. Both dominant species seem to be restricted to environments with a good water quality although no quantitative explorations have been performed on this issue to ascertain also what might be indicators for quality assessment.
Characteristic species:
These include: Rhodophyta (red algae):Titanoderma trochanter, Tenarea tortuosa, Amphiroa rigida, Laurencia obtusa, Haliptilon virgatum, Jania rubens, Lithophyllum incrustans, Neogoniolithon brassica-florida. Phaeophyta: Dictyota fasciola, Padina pavonica, Cystoseira compressa, Cystoseira crinita, Cystoseira barbatula. Chlorophyta (green algae): Anadyomene stellata, Acetabularia acetabulum. Mollusca: Dendropoma petraeum. Fish: Sarpa salpa, Siganus luridus, Parablennius incognitus, Parablennius gattorugine.

Classification:
EUNIS (2007):
Level 4: A sub-habitat of ‘Mediterranean moderate energy infralittoral rock’ (A3.2).
 
Annex 1:
1170 Reefs
 
MAES:
Marine- Marine inlets and transitional waters
Marine- Coastal
 
MSFD:
Shallow sublittoral rock and biogenic reef
 
EUSeaMap:
Shallow photic rock or biogenic reef
 
IUCN:
9.2 Subtidal rock and rocky reefs
 
Barcelona code: 
II. 4. 2. Biocenosis of the lower mediolittoral rock 
II. 4. 2. 3. Association with Tenarea undulosa

Justification Outstanding Example of Biogeographical Region:
The structural species that form this habitat are endemic to the Mediterranean.

Map Description:
This map has been generated using data from IUCN and supplemented with expert opinion. EOO and AOO have been calculated on the available data presented in this map however these should be treated with caution as expert opinion is that this may not indicate the full distribution of the habitat. The habitat distribution is based Herbarium (Algarium) Universitatis Tergestinae Nova collectio - G. Bressan  in CALCHERB on the web site http://dbiodbs.units.it/web/alghe/calc01.

Trends in Quantity:
There is no information on indicators of quantity and trends. Grey literature seems to indicate that some of the reef building species are collected as souvenirs and threatened by other pressures, but the degree of these impacts is unknown.

Trends in Quality:
There is limited information available to evaluate the trends in quality over the last 50 years as research has been focused on taxomic and distribution records rather than trends.

% of Distribution of the Habitat Type within the EU 28:
This habitat has been found at few locations in the Mediterranean and more than 80% of its known distribution is within EU 28.

Justification of Small Range/Regression:
This habitat is present in all the Mediterranean sub-basins therefore it does not have a small natural range.

Justification of Restricted Area:
This habitat is present in all the Mediterranean sub-basins therefore it does not have a small natural range.

Pressures and Threats:
The bioconstructions made by the dominant species, Titanoderma trochanter and Tenarea tortuosa, are threatened by climate induced pressures and collection as souvenirs. Other important threats are coastal habitat modification, sea level rise and pollution but the scale of such pressures is unknown.

Conservation and Management:
Currently, there are no specific conservation actions in place for this habitat.This habitat would benefit from measures to improve the water quality, prevention of removal as souvenirs and establishment of protected areas.

Conservation Status:
Annex 1:
1170:  MMED XX
Titanoderma trochanter and Tenarea tortuosa are both listed in Annex II to the Protocol concerning Specially Protected Areas and Biological Diversity in the Mediterranean of the Barcelona

Capacity to Recover its Typical Character and Functionality?:
Unknown. The rims formed by some of these species only adhere to the substrate at a few points and are easily detached or be broken off by hand. Therefore its recovery capacity will depends on the building of the structure.

Summary:
Little is known about the habitat formed by these rare bioconcretions that are usually found in the infralittoral zone, on well-illuminated, rocky walls exposed to moderate wave action, and occasionally also at mesolittoral level. The small rims formed by Titanoderma trochanter are highly vulnerable to being dislodged by wave action and human activities. The capacity for recovery could be limited. Tenarea tortuosa, is a rare, delicate and elegant species, collected as souvenir and although there are no estimations of this pressure, in some areas it could be high. There are no specific conservation actions in place for this habitat at present. It would however, benefit from measures to improve the water quality, prevention of removal as souvenirs and establishment of protected areas.

References:
Athanasiadis, A. 2008. Morphology, anatomy and reproduction of the eastern Mediterranean coralline Tenarea tortuosa and its relationship to members of the Lithophylloideae and Mastophoroideae (Rhodophyta, Corallinales). Nordic Journal of Botany 15(6): 655-663
Athanasiadis, A., 2003. Taxonomy ofRhodophyta with particular reference to Mediterranean species. - Bocconea 16(1): 193-198.2003. - ISSN 1120-4060. 
AntoliÄ‡ B. et al. 2013. A checklist of the benthic marine macroalgae from the eastern Adriatic coast: IV. Rhodophyta 2: Ceramiales excluded. Actaadriat., 54(1): 41 – 66.
Benhissounea, S., C.-F. Boudouresqueb, M. Perret-Boudouresqueb and M. Verlaqueb, 2002. A Checklist of the Seaweeds of the Mediterranean and Atlantic Coasts of Morocco. III. Rhodophyceae (Excluding Ceramiales). Botanica Marina 45: 391–412.
Bressan, G. & J. Cabioch. 2004. Titanoderma trochanter (Bory) Benhissoume, Boudouresque, Perret-Boudouresque et Verlaque, et Titanoderma ramosissimum Heydrich) comb. nov. (Corallinales, Rhodophytes), une rédefinition. Cahiers Biologie Marine, 45: 225-242.
Huvé, H. 1957. Sur l'individualité générique du Tenarea undulosa Bory 1832 et du Tenarea tortuosa (Esper) Lemoine 1911. Bulletin de la Société Botanique de France, 104: 132-140.
Okudan-Aslan, E. et al. 2014. A new record for the marine algal flora ofturkey: titanoderma trochanter  (bory desaint-vincent) benhissoune, boudouresque,perret-boudouresque and verlaque, 2002(rhodophyta, corallinales, corallinaceae). Fresenus Environmental Bulletin 23(2a): 630-634.

Criterion A Text:
Little is known about the extent and any trends in quantity of this habitat, although some reports seems to indicate of loss in some locations. No estimates have been made of potential future loss of this habitat. The habitat type has therefore been assessed as Data Deficient under Criterion A for both EU 28 and EU 28+.

Criterion B Text:
This habitat has a restricted distribution (AOO <50) and given its vulnerability to climate change and sea level rise, there is a threatening process that is likely to cause a continuing decline in the quantity and/or quality within the next 20 years. This impact will affect the habitat over its whole distribution in the Mediterranean although it is uncertain if some areas will be more resilient than others. This habitat has been assessed as Least Concern under criteria B1b (for both EU 28 and EU 28+), Vulnerable under criteria B2b (for both EU 28 and EU 28+). This habitat has been assessed as Data Deficient under all other criteria.

Criterion C/D Text:
Since there are no studies available on the past and current conditions of this habitat type, it is not possible to calculate the reductions in abiotic and/or biotic quality. The habitat is therefore assessed as Data Deficient under Criterion C/D for both EU 28 and EU 28+.

Criterion E Text:
There is no quantitative analysis available to estimate the probability of collapse of this habitat type. It is therefore assessed as Data Deficient under Criterion E.

Synthesis:
Although this habitat has a wide geographic distribution, it is present in only relatively small areas. Given its vulnerability to climate change and sea level rise, there is a threatening process that is likely to cause a continuing decline in the quantity and/or quality within the next 20 years. This will affect the habitat over its whole distribution in the Mediterranean although it is uncertain if some areas will be more resilient than others. This habitat has therefore been assessed as Vulnerable for both the EU 28 and EU 28+.


Habitat Type Name:
A2.132 Pontic mediolittoral cobbles and gravels

Habitat Description:
This mediolittoral habitat is found in areas of coarse sediment (shingle, cobbles, gravels, shells etc.). These develop in areas of high energy (currents or wave action). As the sediment is quite coarse it typically does not support large volumes of marine life. There may be accumulations of shell hash, for example of Cerastoderma, Mya and other molluscs.
Indicators of quality:
Both biotic and abiotic indicators have been used to describe marine habitat quality. These include: the presence of characteristic species and those which are sensitive to the pressures the habitat may face; water quality parameters; and levels of exposure to particular pressure, and more integrated indices which describe habitat structure and function, such as trophic index, or successional stages of development in habitats that have a natural cycle of change over time.
There are no commonly agreed indicators of quality for this habitat, although particular parameters may have been set in certain situations e.g. protected features within Natura 2000 sites, where reference values have been determined and applied on a location-specific basis.
Characteristic species:
Few species present.

Classification:
EUNIS (v1405):
Level 4. A sub-habitat of Pontic littoral coarse sediment (A2.1).
 
Annex 1:
1160 Large shallow inlets and bays
 
MAES:
Marine - Marine inlets and transitional waters
Marine - Coastal
 
MSFD:
Littoral sediment
 
EUSeaMap:
Not mapped
 
IUCN:
12.3 Shingles and/or pebble shoreline and/or beaches

Justification Outstanding Example of Biogeographical Region:
It is unknown whether this habitat presents an outstanding example of the typical characteristics of the Black Sea region.

Trends in Quantity:
The habitat is most widespread on the eastern coasts of the Black Sea but also occurs sporadically within the EU 28.  There is insufficient data to accurately assess changes in quantity of the habitat.

% of Distribution of the Habitat Type within the EU 28:
It is unknown how much of this habitat is hosted by the EU 28 in the Black Sea, but it is known to occur in other Black Sea countries.

Justification of Small Range/Regression:
The habitat is known to occur in the Black Sea but there is insufficient data to accurately calculate EOO. There is insufficient data to accurately assess whether the habitat has undergone any regression in the last 50 years.

Pressures and Threats:
This habitat is most at risk from coastal developments, including the construction of marinas and slipways, sediment extraction, the widening and dredging of channels, creation of artificial beaches, road building and sea defenses. These activities may alter the hydrological regime which will in turn affect the character and viability of the habitat. Other potential pressures are from pollution (chemical and plastic) and eutrophication which may affect the associated species.

Conservation and Management:
Protection from the direct and indirect effects of coastal development will benefit this habitat as well as pollution control and regulation, water quality management, contingency plans to be followed in the event of a major pollution incident.

Capacity to Recover its Typical Character and Functionality?:
There is insufficient data and knowledge of this habitat to assess its capacity to recover.

Summary:
The habitat is present in the Black Sea on areas of mediolittoral cobbles and gravel in high energy environments. It is also present in the Sea of Marmara. As the sediment is quite coarse it typically does not support large volumes of marine life. Eutrophication is the most significant historic pressures affecting this habitat. Additional pressures include coastal development, chemical pollution and plastic pollution. Conservation measures which will benefit the habitat include restoring the biological and physical integrity, improvements to water quality, coastal development controls and contingency plans in case of a pollution event.

References:
Anon. 2006. The northwestern part of the Black Sea: biology and ecology. Kiev: Naukova Dumka. 701pp.
Bacescu, M. C., Muller G. I., Gomoiu, M-T. 1971. . Cercetari de ecologie bentica in Marea Neagra (analiza cantitativa, calitativa si comparata a faunei bentice pontice). Ecologie Marina vol. IV. Editura Academiei R.S.R., Bucuresti, 357 pp..
Bacescu M., 1977. Les biocenoses benthiques de la Mer Noire.  Biologie des eaux saumatres de la Mer Noire, Premiere partie: 128-134.
Çulha, M., Bat, L., Türk Çulha, S. & Çelik, M.Y. 2010. Benthic mollusk composition of some facies in the upper-infralittoral zone of the southern Black Sea, Turkey. Turkish Journal of Zoology 34: 523-532.
Dimitrova-Konaklieva, S. 2000. Flora of the Marine Algae of Bulgaria (Rhodophyta, Phaeophyta, Chlorophyta). Pensoft, Sofia, Bulgaria.
Gönlügür Demirci, G. 2005. Sinop YarÄ±madasÄ±nÄ±n (Orta Karadeniz) Mollusca FaunasÄ±. Science and mEngineering Journal of FÄ±rat University17(3): 565-572.
Kalugina-Gutnik A.A. 1970. The composition and distribution of benthic vegetation in the south-eastern part of the Black Sea. Ecological and morphological studies of benthic organisms. Kiev: Naukova Dumka, p. 185- 202.
Kiseleva, M. I. 1981. Benthos of Black Sea mobile substrates. Naukova dumka, Kiev, pp 165.
Konsulov, A. 1998. Black Sea Biological Diversity: Bulgaria. Volume 5 of Black Sea environmental series. United Nations Publications, New York, USA.

Criterion A Text:
There is insufficient data on changes in quantity of this habitat. This habitat is therefore assessed as Data Deficient under criterion A.

Criterion B Text:
This habitat occurs in the Black Sea but there is insufficient data to calculate EOO and AOO. This habitat has therefore been assessed as Data Deficient under criterion B.

Contributors:
S. Beal, G. Komakhidze, V. Kopiy, D. Micu, V. Mihneva, N. Milchakova, B. Yokes


Habitat Description:
These are coniferous woodlands of shallow to deep peats and peaty mineral soils sustained by high ground water in gentle depressions on plains, on river terraces and at the margins of treeless mires throughout the boreal and more locally in the nemoral zones. Picea mire woodland can occur on ombrotrophic active bog surface on deep peat, but is more often found on minerotrophic peats or on shallower peaty soils at mire margins, though in drier regions being more extensive on the mire surface. Tree cover can be sparse with low-growing individuals when the associated flora is very similar to the open bog or mire surface while, under more closed canopies, shade-tolerant species prevail. An uneven age structure among the trees is characteristic of natural sites. Picea abies tends to be the canopy dominant in extensive stands on a hummock-dominated peat surface, or sometimes a more pronounced hummock-hollow micro-topography on the peat surface. Sometimes Abies alba is (co-)dominant in more minerotrophic conditions. Betula pubescens, Pinus sylvestris and Salix spp. are common associates sometimes with Alnus glutinosa and A. incana admixed in somewhat less oligotrophic situations. Picea abies ssp.obovata is a dominant subspecies vicariating with P. abies ssp. abies  in northeastern parts of Europe. The field layer has such dwarf shrubs as Vaccinium myrtillus, V. vitis-idaea, V. uliginosum, V. oxycoccos, Ledum palustre, Chamaedaphne calyculata, with herbs and sedges like Melampyrum pratense, Rubus chamaemorus, Eriophorum vaginatum, Carex globularis as well as  peat-forming Sphagna like S. angustifolium, S. centrale, S. girgensohnii,  S. palustre,  S. magellanicum and S. russowii with big pleurocarpous mosses on drier hummocks. In more mesothrophic conditions, herbs like Equisetum sylvaticum, Dryopteris carthusiana, Trientalis europaea, and graminoids like Calamagrostis purpurea, Carex canescens and Carex loliacea are common. Trickles of moving water can even sustain species such as Calla palustris, Menyanthes trifoliata, Equisetum fluviatile, E. palustre and Comarum palustre.
Indicators of quality:
•       No forest exploitations.
•       Intact natural mire hydrology.
•       Natural composition of canopy with dominant Picea spp.
•       Structural diversity/ -complexity with (semi)natural age structure or completeness of layers.
•       Presence of old trees and a variety of dead wood (lying or standing) and the associated flora, fauna and fungi.
•       Presence of natural disturbance such as treefall openings with natural regeneration.
•       Long historical continuity (ancient woodland) with high species diversity.
•       Survival of larger stands of forest without anthropogenic fragmentation and isolation.
•       Absence of non-native species in all layers (flora and fauna).
•       No signs of eutrophication or pollution.
Characteristic species:
Tree canopy: Picea abies, Abies alba, Betula pubescens, Alnus incana, A. glutinosa, Frangula alnus.
Field layer: Vaccinium myrtillus, V. vitis-idaea, Vaccinium uliginosum, V. oxycoccos, Ledum palustre, Chamaedaphne calyculata, Calluna vulgaris, Empetrum nigrum, Calamagrostis purpurea, Carex canescens, C. globularis, C. loliacea, C. nigra, Andromeda polifolia, Equisetum sylvaticum, Dryopteris carthusiana, Melampyrum pratense, Drosera rotundifolia, Rubus chamaemorus, Trientalis europaea.
Bryophytes: Sphagnum capillifolium, S. centrale, S. fallax, S. flexuosum, S. palustre, S, magellanicum, S. girgensohnii, S. russowii, S. squarrosum, Dicranum majus, Polytrichum commune, P. strictum, Mylia anomala, Aulacomnium palustre, Barbilophozia lycopodioides.

Classification:
EUNIS:
G3.D Boreal bog conifer woodland
G3.E Nemoral bog conifer woodland
EuroVegChecklist alliances:
Empetro-Piceion obovatae Morozova et al. 2008
Eriophoro-Piceion abietis Passarge 1968
Calamagrostio canescentis-Piceion abietis Solomeshch in Solomeshch et Grigorjev 1992 nom. inval.
Annex I:
91D0 Bog woodland
Emerald:
G3.D Boreal bog conifer woodland
G3.E Nemoral bog conifer woodland
MAES-2:
Woodland and forest
IUCN:
1.1 Boreal Forest
1.4 Temperate Forest
EFT:
11.1 Conifer dominated or mixed mire forests
VME:
D1 Western boreal spruce forests, Boreal and hemiboreal pine forests

Justification Outstanding Example of Biogeographical Region:
This is an azonal habitat type distributed in several biogeographic regions.

Map Description:
The map is very incomplete, and therefore the potential distribution (based on Annex I type 91D0) is given for the EU. Data sources: EVA, Art17.

Comment EU28:
The area is without countries which gave  data on G3.D/E only

Comment EU28+:
The area is without countries which gave  data on G3.D/E only

Trends in Quantity:
There was a 51% decrease in the EU 28 region during the past 50 years, calculated with trend data based on all countries except Austria, Latvia and Lithuania. Calculating trends in quantity for the EU 28+ region was not possible, since trend data were missing from Norway, where a relatively large part of the area of this habitat may lie. The greatest decrease (70%) occurred in Finland, which also has the second largest area of this habitat. The most important reason for the decline by far has been the drainage of peatlands for forestry. There are no historical data from 250-50 years ago. The area of the habitat is currently stable, as new peatland sites are not drained anymore in the Northern Europe.
Austria, Romania, Slovenia, Norway, Slovakia and France have reported this type and G3.Da Pinus mire woodland combined together. For these countries areas above are given in the form 0-total, i.e. assuming that the area could be anything from 0 km2 to the total reported by the country. Trend calculations for the EU 28 were made using both 0 km2 and the total reported for these countries. The result did not differ much, since all of these countries except Norway had a very small area of this type.
In the territorial data of some countries it is unclear whether drained mires are included in the reported area or not. For instance, in the territorial data of Sweden the decrease of the area is only 1,2% in the past 50 years, even though it is known that some drainage has occurred during that time period. On the other hand, the territorial data of Finland reports area of undrained mires only, which explains the drastic decline.

Trends in Quality:
In the past 50 years there has been a slight decline (31% relative severity) affecting 33% of the extent of the habitat in the EU 28, calculated based on trend data for all countries except Austria, Slovakia, Italy, Estonia, Latvia, Lithuania and Poland. It was not possible to calculate a qualitative trend for EU 28+, as trend data on habitat quality for Norway was missing, and a relatively large area of this habitat type may occur there. The degradation of this habitat type has been both abiotic and biotic. The most important reasons for the decline in quality have been drainage of peatlands for forestry and forest cuttings. The current trend is decreasing in most countries, and it is possible that in the future climate change will also have negative effects on the quality of this habitat.

% of Distribution of the Habitat Type within the EU 28:
Less than 50 % of the current distribution of the habitat lies within the EU 28. There are large areas of this habitat in Russia, and the habitat is also present in some other countries outside the EU 28.

Pressures and Threats:
Drainage of peatlands for forestry, forest cuttings, eutrophication due to pollution (especially on ombrotrophic and oligotrophic sites), infrastructure development and climate change are the main threats to this habitat. However, in many countries ditching of hydrologically intact peatland sites is not practiced any more. Stands of this habitat type are usually more intensively managed by forestry than those of the habitat G3.Da Pinus sylvestris mire woodlands, but there is not much scientific knowledge available on development of peatland ecosystems with developing secondary stands after clear-cutting. The influence of climate change is likely to increase in the future.

Conservation and Management:
The most common approaches currently involve establishing protected areas/sites, establishing wilderness areas, restoring/improving habitats, usually by restoring hydrological conditions, and adapting forest management. Some of the additional actions needed include further optimizing the use of funds for conservation (what kind of areas are chosen for conservation and where), further improving methods for conservation/nature management in managed forests (e.g. regarding deadwood), adaptation of spatial planning (roads, etc.), and bringing climate change under control.

Conservation Status:
Annex I:
91D0: ALP FV, ATL U2, BOR U1, CON U1, MAC U1, PAN U1

Capacity to Recover its Typical Character and Functionality?:
The habitat has the potential to recover, but recovery will be very slow. It always requires restoration of hydrological conditions.

Summary:
This habitat comprises Picea abies woodland on shallow to deep peats and peaty mineral soils sustained by high ground water in gentle depressions on plains, on river terraces and at the margins of treeless mires throughout the boreal and more locally in the nemoral zones. An uneven age structure among the trees is characteristic of natural sites but tree cover can be sparse with low-growing individuals when the associated flora is very similar to the open bog or fen surface while, under more closed canopies, shade-tolerant species prevail. Sometimes Abies alba is (co-)dominant in more minerotrophic conditions and other trees can occur. The field layer has dwarf shrubs, peat-forming Sphagna, big pleurocarpous mosses on drier hummocks, in more mesotrophic conditions, herbs and graminoids and, where there are trickles of moving water, semi-aquatic plants. Drainage of peatlands, forest cuttings, eutrophication due to pollution, infrastructure development and climate change continue to be the main pressures. Protected areas, maintenance of hydrology and improved forestry are conservation needs.

Criterion A Text:
During the past 50, there has been a 51% reduction in the quantity of this habitat in the EU 28 based on territorial data. The habitat is therefore assessed as Endangered under criterion A1. Data on quantitative trends in Austria, Latvia, Lithuania, Norway and Serbia are missing. A relatively large area of this habitat type may lie within Norway. Therefore, the habitat is assessed as Data Deficient under criterion A in the EU 28+ region. There is no information on future or historic reductions for this habitat type.

Criterion C/D Text:
In the past 50 years, 33 % of the habitat area in the EU 28 was affected by a slight reduction in quality (31% relative severity), and the habitat is therefore assessed as Least Concern under criteria C/D1. The type of quality degradation usually was both abiotic and biotic. A majority of the area with reduced quality was affected with slight severity. Trend data of qualitative degradation were missing in Austria, Estonia, Italy, Latvia, Lithuania, Norway, Poland, Serbia, and Slovakia. A relatively large part of the area of this type may lie within Norway, and this habitat is, therefore, assessed as Data Deficient under Criterion C/D in EU 28+.

Synthesis:
The habitat is assessed as Endangered under criterion A1 in the EU 28, as there has been a 51% decline in its quantity within the last 50 years. However, the area of the habitat is currently stable, as drainage of new peatland sites for forestry is not practiced any more in Northern Europe. There has also been a slight decline in the quality of this habitat, affecting 33% of its extent in the EU 28 in the last 50 years. The habitat quality continues to decrease in most EU 28 countries. Trend data on reduction in quantity were missing from Austria, Latvia, Lithuania, Norway and Serbia. Trend data on reduction in quality was missing from Austria, Estonia, Italy, Latvia, Lithuania, Norway, Poland, Serbia and Slovakia. Six of the countries (including Norway) reported their data of this type combined with the type G3.Db Pinus mire woodland. This habitat type is assessed as Data Deficient at the EU 28+ since a relatively large part of its area may lie within Norway, but precise values are unknown due to the combination of this habitat type with type G3. Db Picea mire woodland. Classification of spruce-dominated peatland forests varies between the countries, and there is a risk that providers of territorial data do not have a common understanding about what kind of habitats are included in this type.

Contributors:
Type description: J. Rodwell & A. Ssymank
Territorial data: S. Armiraglio, S. Assini, L. Aunina, E. Bendiksen, C. Bita-Nicolae, G. Buffa, A. Carni, M. Chytry, J. Dahlgren, R. Delarze, M. Dimitrov, P. Finck, N. Juvan, Z. Kacki, T. Kontula, V. Rasomavicius, U. Raths, B. Renaux, U. Riecken, I. Sell, A. Ssymank, V. Stupar, M. Valachovic, W. Willner
Working Group Forests: F. Attore, R-J. Bijlsma, M. Chytrý, P. Dimopoulos, B. Renaux, A. Ssymank, T. Tonteri, M. Valderrabano


Habitat Description:
Boreal ultramafic inland cliffs are habitats which host unique serpentine plant communities. The concept ultramafic refers to rock types that have a low content of silica and rather high content of magnesium and iron. This kind of rock, in particular serpentinite, produces extreme edaphic conditions with low calcium-to-magnesium ratio, severe scarcity of essential nutrients such as nitrogen, potassium, and phosphorus, and often also high levels of heavy metals such as nickel, chromium or cobalt. As a consequence of these chemical conditions, vegetation is often very scarce with large spots of bare rock. As an adaptation to harsh environment some species have developed morphological features of dry site plants.
Some plants have adapted to these harsh conditions. In the Boreal region, this group includes Arenaria pseudofrigida, Asplenium adulterinum, A. viride, Cerastium alpinum, C. fontanum ssp. vulgare, Dianthus superbus, Minuartia biflora, Sagina nodosa and Viscaria alpina var. serpentinicola. In addition to these special plants, some common plants also grow in serpentine environments, e.g. Calluna vulgaris, Juniperus communis, Deschampsia flexuosa, Festuca ovina and Sedum telephium.
Bryophyte and lichen communities of serpentine cliffs often show a special mixture of calciphilous and other species. Typical bryophytes include Campyliadelphus chrysophyllus, Encalypta streptocarpa, Sanionia uncinata, Schistidium apocarpum coll., Tortella tortuosa and Weissia controversa, but in contrast to calcareous cliffs they do not form luxuriant turfs. Both bryophyte and lichen vegetation cover is generally lower than on other kinds of rocks and large areas on rock walls are entirely unvegetated.
The relationship between serpentine plant communities and rock types is under discussion. All ultramafic rock types do not host distinct serpentine plant communities. For example, communities on unchanged peridotite usually resemble those of ordinary siliceous cliffs more than serpentine cliffs.
Ultramafic cliffs with serpentine plant communities occur from the lowlands of eastern Finland to the middle alpine zone of the Scandinavian mountains. Two vegetation types have been recognized: the more widespread Asplenium viride – Arenaria norvegica–type (with a variant without A. norvegica in the eastern parts of the region) and the oceanic Asplenium adulterinum–type.
Indicators of good quality:
bedrock intact (no quarrying)
presence of natural disturbance regime (relevant especially in forested areas: forest fires are prevented, which means that vegetation coverage is slowly increasing; on the other hand, intensive forestry and particularly clearcutting causes abrupt changes in microclimate, which destroy plant communities adapted to stable humid conditions)
absence of alien species

The species diversity varies enormously also in entirely natural communities in cliff habitats. Usually, the smallest rock formations with monotonous microtopography and little variation in rock types show low diversity, whereas larger cliff complexes with heterogeneous geomorphology and varying rock types may represent local biodiversity hotspots. Therefore, low species diversity or absence of rare species should not be interpreted by itself as an indicator of low habitat quality, unless it is caused by anthropogenic influence.
Characteristic species:
Flora:
Vascular plants: Agrostis stolonifera, Arenaria humifusa, A. norvegica, A. pseudofrigida, Asplenium adiantum-nigrum, A. adulterinum, A. trichomanes, A. viride, Calluna vulgaris, Campanula rotundifolia, Cardaminopsis petraea, Cerastium alpinum and its subspecies, C. fontanum var. kajanense, C. nigrescens subsp. nigrescens, Festuca ovina, Juncus trifidus, Luzula spicata, Minuartia biflora, M. rubella, Molinia caerulea, Rumex acetosa var. serpentinicola, Silene dioica, S. uniflora, Trichophorum caespitosum, Viscaria alpina var. serpentinicola (=Silene suecica var. serpentinicola).
Bryophytes: Brachythecium velutinum, Bryum nitidululm, Campyliadelphus chrysophyllus, Ditrichum flexicaule, Encalypta streptocarpa, Sanionia uncinata, Schistidium apocarpum coll., Tortella tortuosa, Weissia controversa, Zygodon spp.
Lichens: Lichens of serpentine cliffs are not well known in the Boreal zone. These species were found to be characteristic in the Finnish studies of serpentine cliffs:
Calvitimela aglaea, Fuscopannaria leucophaea, Micarea erratica, Miriquidica complanata, Phaephyscia endococcina, Physconia muscigena, Protopannaria pezizoides.
Additionally on slightly more calcareous serpentine cliffs: Botryolepraria lesdainii, Caloplaca obliterans, Candelariella vitellina, Fuscopannaria praetermissa, Heterodermia speciosa, Physcia tenella, Physconia perisidiosa, P. detersa, Protoparmeliopsis muralis, Ramalina pollinaria, Xanthoparmelia somloënsis, Xanthoria elegans

Classification:
EUNIS:
H3.2 Basic and ultra-basic inland cliffs
EuroVeg Checklist:
Asplenion serpentini Br.-Bl. et Tx. ex Eggler 1955
Annex 1:
8220 Siliceous rocky slopes with chasmophytic vegetation (The Annex 1 habitat type 8220 is defined as to correspond, among others, to the unit “713 Klippvegetation på Serpentinbergarter“ of the Nordic classification).
Emerald:
H3.2 Basic and ultra-basic inland cliff
MAES-2:
Sparsely vegetated land
IUCN:
6. Rocky areas

Justification Outstanding Example of Biogeographical Region:
Ultramafic cliffs with serpentine plant communities occur from the lowlands of eastern Finland to the middle alpine zone of the Scandinavian mountains.

Map Description:
The map gives an underestimate of the distribution due to data gaps. Data from Finland is lacking completely. Data sources: LIT, GBIF.

Trends in Quantity:
These specific cliffs and ridges are supposed to have a relatively stable trend in quantity, although some threats, e.g. degradation due to intensive pasturing and fertilisation near rocky outcrops may reduce the total area of the habitat. The calculation of trends was not possible due to a lack of relevant data.

Trends in Quality:
The calculation of trends in quality was not possible due to a lack of important data. The ultramafic rocks host a lot of specialists and stenoendemic plant species. Therefore, there is a high probability that a negative future trend will lead to a decrease in the species pool.

% of Distribution of the Habitat Type within the EU 28:
The habitat type occurs only in Finland, Norway, and Sweden. The stated current area in Sweden is only a raw estimate based on data by Rune (1953). It is not possible to provide a percentage quotation due to a lack of data.

Justification of Small Range/Regression:
A small local decline can be registered, but generally is more or less stable. There is no information available concerning EOO.

Justification of Restricted Area:
This habitat type has only local and small occurrence inside of the relatively large total distribution.

Pressures and Threats:
Serpentine soils are rich in heavy metals, they are calcium-poor, and nutrient availability is very limited, therefore they represent very special isolated habitats for plants. The spatial isolation may make it much more difficult for plant species to successfully migrate when conditions (such as climate) will change. Under stable conditions, this habitat shows also a stability and edaphic endemism. If generalists can move through continuous habitats to reach a newly suitable habitat, specialists, such as serpentine endemics must make large jumps to disperse from one suitable habitat patch to another. They have to cross areas of unsuitable habitats and have to deal with a decreasing likelihood of successful dispersal (Damschen et al. 2012). The most significant threats are: (1) environmental changes, e.g. climate changes; (2) degradation of soils due to intensive pasturing and fertilisation of soils; (3) mining and quarrying as a direct liquidation of rocks; (4) afforestation.

Conservation and Management:
The habitats on ultramafic rocks are relatively stable, although some threats, e.g. degradation due to intensive pasturing and fertilisation near rocky outcrops can reduce the total area of the habitat. The management of those habitats requires an exclusion of direct inputs such as climbing and trampling. The best management policy is to protect these habitats as natural reserves.

Capacity to Recover its Typical Character and Functionality?:
if severely demaged, the recovery of the habitat will take a very long time, more than 200 years.

Summary:
This ultramafic inland cliff habitat occurs in the boreal zone of Scandinavia only. Though the total distribution is still unclear, it is considered very rare. It is characterised by a boreal flora of vascular plants and ferns specialised for the serpentine substrate with its distinctive mineral content and by bryophyte and lichen assemblages that are partly typical of calcareous habitats, though not here forming any luxuriant cover. Although the condition of the habitat is poorly known, it is threatened by climate change, degradation of soils due to intensive pasturing and fertilisation of soils, mining and quarrying and afforestation.

References:
Damschen, E.I., Harrison, S., Ackerly, D.D., Fernandez-Going, B.M. and Anacker, B.L. 2012. Endemic plant communities on special soils: early victims or hardy survivors of climate change? Journal of Ecology 100: 1122–1130.
Norokorpi, Y., Eeronheimo, H., Eurola, S., Heikkinen, R., Johansson, P., Kumpula, J., Mäkelä, K., Neuvonen, S., Sihvo, J., Tynys, S. and Virtanen, R. 2008. Tunturit Suomen luontotyyppien uhanalaisuus (Assessment of Threatened Habitat Types in Finland), pp. 467-541. In: Raunio, A., Schulman, A. and Kontula, T. eds. Suomen luontotyyppien uhanalaisuus: Osa 2: Luontotyyppien kuvaukset. Suomen ympäristökeskus, Helsink, Finnish Environment Institute, Helsinky, 572 p.
Rune, 0. 1953. Plant Iife on serpentines and related rocks in nord Sweden. Acta Phytogeographica Suecica 31: 1-139, Uppsala.

Criterion A Text:
Trend data have been reported only from Finland (-5% decline). Therefore no reliable European trend could be estimated more EU28 (especially Swedish data needed) or EU28+ (Swedish and Norwegian data needed).

Criterion B Text:
The provided AOO and EOO are very low (AOO < 50), but very few data were available for the distribution map. It is expected that with better data EOO values are larger than the thresholds for criterion B1 and B2. The same goes for the AOO value for the EU28+, but this is less certain for the EU28 (and therefore indicated as unknown). Also the number of locations is higher than the threshold for B3.

Criterion C/D Text:
The calculation of trends in quality was not possible due to absence of reliable data.

Synthesis:
The habitat has been assessed as Data Deficient (DD) due to missing detailed information on distribution, area and trends. Due to a lack of important data from Sweden and Norway, the calculation of trends in quality and quantity was not possible. Therefore, these criteria have not been evaluated.

Sub-habitats in Need of Examination:
The habitat type corresponds partly with serpentine rock outcrops and screes or with mountain ultramafic bedrock outcrops and boulder fields; therefore, some sub-types which require further examination can be expected. In the Nordic classification, thi

Contributors:
Habitat definition: T. Kontula
Territorial data: T. Kontula
Working Group Sparsely Vegetated Habitats: F. Essl, G. Giusso Del Galdo, A. Mikolajczak, D. Paternoster, M. ValachoviÄ, M. Valderrabano


Habitat Type Name:
D4.1a Small-sedge base-rich fen and calcareous spring mire

Habitat Description:
This habitat includes calcareous fen vegetation of the lowlands and mountains of the European nemoral zone, and it also occurs more rarely in the boreal zone where calcareous substrates and the influence of base-rich water are scarce. Calcareous fens occur at sites with a permanently high water table, often near springs, and they are particularly common in areas with calcareous bedrock, especially in the mountain systems of central Europe. Water is rich in calcium, magnesium and bicarbonates and precipitation of calcium-carbonate and tufa formation is common, and also accumulation of organic matter due to permanently wet conditions which reduce decomposition processes. The soil has a high proportion of organic matter and is base-rich, but with limited availability of nutrients.
The vegetation of base-rich fens is dominated by small sedges such as Carex davalliana, C.  flava, C. hostiana, C. lepidocarpa and other short or medium-tall Cyperaceae such as Blysmus compressus, Eleocharis quinqueflora, Eriophorum angustifolium and E. latifolium. In some places these species typical of fens grow together with species characteristic of wet meadows on mineral soil such as Anthoxanthum odoratum, Briza media, Caltha palustris, Cirsium palustre, C. rivulare, Cynosurus cristatus, Festuca rubra agg., Holcus lanatus, Lychnis flos-cuculi, Plantago lanceolata and Ranunculus acris. Bryophytes are common, in some stands reaching a cover close to 100% and, in the moss layer, species of fens (e.g. Bryum pseudotriquetrum, Campylium stellatum, Hamatocaulis vernicosus, Palustriella commutata and Scorpidium cossonii) can grow together with species typical of mineral soils (e.g. Cirriphyllum piliferum, Climacium dendroides, Plagiomnium affine agg., Rhytidiadelphus squarrosus), although the latter may be absent at some sites, especially in primary fens.
Small-sedge calcareous fens can be primary habitats developed around springs and seepages of calcium-rich water. Some of them can be several thousand years old and the long-term habitat continuity can be indicated by the occurrence of species such as Primula farinosa, Salix rosmarinifolia or Triglochin maritimum. At some sites, however, fens can be natural but only a few centuries old, and in other sites they can be secondary, developed on formerly forested land and be dependent on regular mowing. Many of them have been mown once a year without input of fertilizers for several centuries. Export of nutrients with hay has led to partial elimination of nutrient-demanding tall-growing species of wet meadows. Many of these species are still growing in these grasslands but their competitive ability is too weak to outcompete short-growing fen species. Small-sedge fens are most common and most diverse in the limestone massifs of the central European mountain systems, especially the Alps and the Carpathians.
In many places calcareous fen meadows have been damaged or destroyed by artificial drainage, which has caused mineralization of nutrients in the fen sediment and the spread of nutrient-demanding species of wet meadows or species of strongly-drained mesic meadows. To some extent they can be negatively influenced by livestock grazing as well.
Indicators of good quality:
In general, primary fens without species of wet meadows are more valuable than secondary fens. However, in some areas, especially in the lowlands, primary fens may not occur and in that case the secondary fens with meadow species have the highest conservation value.
·      Stable hydrological regime
·      Continued traditional management at secondary habitats
·      Absence of overgrazing
·      No encroachment of trees or shrubs
·      No spread of tall-growing nutrient-demanding herbs
·      Absence or low incidence of neophytes
Characteristic species:
Flora: Vascular plants: Anthoxanthum odoratum, Aster bellidiastrum, Bartsia alpina, Blysmus compressus, Briza media, Caltha palustris, Carex davalliana, Carex flava, Carex hostiana, Carex lepidocarpa, Cirsium palustre, Cirsium rivulare, Crepis paludosa, Cruciata glabra, Cynosurus cristatus, Dactylorhiza incarnata, Dactylorhiza majalis, Eleocharis quinqueflora, Epipactis palustris, Eriophorum angustifolium, Eriophorum latifolium, Festuca rubra agg., Galium uliginosum, Holcus lanatus, Juncus alpinoarticulatus, Juncus effusus, Lathyrus pratensis, Lychnis flos-cuculi, Menyanthes trifoliata, Parnassia palustris, Pinguicula vulgaris, Plantago lanceolata, Primula elatior, Primula farinosa, Prunella vulgaris, Ranunculus acris, Scirpus sylvaticus, Selaginella selaginoides, Tofieldia calyculata, Trichophorum cespitosum, Triglochin palustris, Valeriana dioica, Valeriana simplicifolia
Mosses: Bryum pseudotriquetrum, Calliergonella cuspidata, Campylium stellatum, Cirriphyllum piliferum, Climacium dendroides, Cratoneuron filicinum, Hamatocaulis vernicosus, Palustriella commutata, Palustriella falcata, Plagiomnium affine agg., Rhytidiadelphus squarrosus, Scorpidium cossonii, Thuidium philibertii

Classification:
EUNIS:
D4.1 Rich fens, including eutrophic tall-herb fens and calcareous flushes and soaks
EuroVegChecklist:
Caricion davallianae Klika 1934
Caricion viridulo-trinervis Julve ex Hájek et Mucina in Theurillat et al. 2015
Sphagno-Tomentypnion Dahl 1956 (marginally)
Annex I:
7230 Alkaline fens
Emerald:
D4.1 Rich fens, including eutrophic tall-herb fens and calcareous flushes and soaks
MAES-2:
Wetlands
 IUCN:
5.4.  Bogs, Marshes, Swamps, Fens, Peatlands

Justification Outstanding Example of Biogeographical Region:
The most typical examples with greatest concentration of habitat specialists occur in the Alps and Carpathians. Large areas are reported also from Scandinavian countries.

Map Description:
As for other mire habitats, the largest areas are reported from Scandinavia and Ireland. Nevertheless, this habitat is quite common in the Alps and Carpathians as well, where it occurs as the most typical sub-type. It occurrs also in lower altitudes in temperate Europe and extends southwards to the Balkans, Apennines and Spanish mountains. Spring hydrology and calcium-rich bedrock are good determinants of its occurrence.
The map is complete for EU28, but incomplete for Norway, the Balkan and possibly Iceland.

Trends in Quantity:
During last decades, most of these fens have disappeared from agricultural landscapes, including semi-natural mountain landscapes such as the Alps. The trend is the same in northern Europe, with regions experiencing strong decline occurring northwards to Central Sweden, including all the Baltic region. Decline is continuing even in nature reserves because of overall eutrophication of the landscape, water table decline and lack of management. Less declining are fens in alpine zones.

Trends in Quality:
Quality is still declinining, even in protected landscapes. Loss of habitat specialists have been repeatedly reported even from protected areas with active management and it is difficult to fix it. The habitat is changing into wet grasslands with an increase of generalist wetland and grassland species, reed beds or alder and willow carrs.

Justification of Small Range/Regression:
Still ongoing. Decline of small-sedge fens, especially those limited by phoshorus (Caricion davallianae) are still not fixed. Even in some protected areas these fens are changing into Sphagnum fens, reed beds or broadleaved wet grasslands.

Justification of Restricted Area:
The habitat requires high calcium content (a rather rare phenomenon in the regions richest in peatlands), low nutrient availability and stable high water level.  A regional stability of the habitat at a millenial scale is important as well.</

Pressures and Threats:
The main threats are connected with increasing nutrient input (especially phosphorus) and drainage. Because many of these fens are small, also direct destruction by developmental activies is frequent. Increasing nutrient input (diffuse groundwater pollution especially) and water table decline leads to succession towards poor or intermediate fens, reed beds (Phragmites australis) or broadleaved wet grasslands. Management may slow down or block the succession and hence counteract the undesired succession, so cessation of management is also a threat. Some territorial data report lack of grazing as a threat, but the effect of grazing is equivocal - if it leads to increasing nutrient input, succession may continue or even accelerate, especially when grazing has ceased temporarily. On the other hand, grazing creates surface disturbance supporting some rare species. Generally, once-a-year mowing is the best way to block succession on sites with decreased water table and increased nutrient content.

Conservation and Management:
The following procedures are advised:
No intervention - in boreal or high mountain fens, with stable high water level, no extra supply of nutrients and no invasive species.
Mowing - in fens enriched in nutrients or with declining water level, typically in young habitats with shallow peat level that has developed since Middle Ages. Also in fens invaded by Molinia, Phragmites, Calamagrostis, Filipendula or tall willows. Additional spring mowing can supress invasive grasses such as Molinia or Phragmites, should not be applied permanently
Grazing - with caution only, may bring extra nutrients.
Artificial disturbances -  if acidicole, late-successional Sphagnum species invade, disturbances without nutrient input (e.g., removal of expanding peat mosses) may be applied to support original brown-moss vegetation.
Extensive restoration measures (blocking drainage channels, sod removal) - in heavily damaged fens.

Conservation Status:
Annex I:
7230: ALP U1, ATL U2, BOR U1, CON U2, MED U2, PAN U2

Capacity to Recover its Typical Character and Functionality?:
Naturally only if habitat specialists survived at site, nutrient availability is not increased and water regime is unaffected.
Through intervention restoration is extremely difficult as demonstrated by several studies, especially because of problems with nutrient oversupply, iron toxicity and cessation of carbonate precipitation during water level manipulations

Summary:
This habitat includes short-sedge fens, spring fens and fen grasslands kept continually wet by base-rich, nutrient-poor waters, occurring through the lowlands and mountains of nemoral Europe and more locally in the boreal zone. They are most common, rich and diverse in the limestone massifs of central European mountains, especially the Alps and Carpathians. Some are primary, developing around natural springs and seepage lines, and may be extremely old, while other vegetation included here has developed on suitably wet ground within the forest zone and been maintained by mowing which depletes nutrients. The soil is rich in organic matter and has high pH, often with precipitation of carbonate or tufa. Small basiphilous sedges dominate the vegetation with a rich associated flora and a patchy carpet of fen bryophytes. Grazing animals often help maintain an open surface favouring high diversity. Eutrophication from surrounding farmland or by atmospheric deposition, interference with the hydrology and invasion of competitive plants pose threats to this habitat which is not readily restorable. Because it serves as a refugium for many plant and invertebrate species, its protection from further damage is urgent.

References:
Bergamini, A., Peintinger, M., Fakheran, S., Moradi, H., Schmid, B. and Joshi, J. 2009. Loss of habitat specialists despite conservation management in fen remnants 1995–2006. Perspectives in Plant Ecology, Evolution and Systematics 11(1): 65-79.
Essl F., Dullinger S., Moser D., Rabitsch W., Kleinbauer I. 2012. Vulnerability of mires under climate change: implications for nature conservation and climate change adaptation. Biodiv. Cons. 21: 655–669
Hájková, P., Horsák, M., Hájek, M., Jankovská, V., Jamrichová, E., Moutelíková, J. 2015. Using multi-proxy palaeoecology to test a relict status of refugial populations of calcareous-fen species in the Western Carpathians. The Holocene 25(4): 702-715.
Jiménez-Alfaro, B., Hájek, M., Ejrnaes, R., Rodwell, J., Pawlikowski, P., Weeda, E. J., Laitinen, J., Moen, A., Bergamini, A., Aunina, L., Sekulová, L., Tahvanainen, T., Gillet, F., Jandt, U., DítÄ›, D., Hájková, P., Corriol, G., Kondelin, H., Díaz, T. E. 2014. Biogeographic patterns of base-rich fen vegetation across Europe. Applied Vegetation Science 17: 367-380.
Moen, A., Lyngstad, A. and Øien, D. I. 2012. Boreal rich fen vegetation formerly used for haymaking. Nordic Journal of Botany 30(2): 226-240.

Criterion A Text:
Decline 50.4% (recent trend EU28) and 67% (historical trend) is calculated from the average of estimations of territorial experts, but without including declines in Belgium, Croatia, Greece, Ireland, Latvia, Romania and United Kingdom where no trend data are available. If estimation based on similar countries (in terms of land use and environmental conditions) is applied, total decline is about 52%. When the same simulation is used for historical trend, the long-term decline will reach ca. 70%. Some uncertainty is imputed by the extremely large area reported for Sweden, almost one half of total European area, with rather low decline reported (ca. 20%) and no estimation for historical decline which was substantial because of drainage already since late 1800s. The delimitation of short-sedge fens is less clear in Central Sweden (from where largest area and lowest decline are reported) with many transitions towards calcareous quaking fens and tall-sedge calcareous fens and absence of some indicators of small-sedge calcareous fens. The real declines are probably higher than reported here, especially for historical trend. The classification into the Endangered (EN) category hence seems clear and realistic.

Criterion B Text:
EOO, AOO and number of locations are far beyond the thresholds for criterion B1, B2 and B3.

Criterion C/D Text:
Percentages are based on territorial data provided by local experts. Among countries reporting large areas of this habitat, no data were provided from Estonia (where severe degradation is expected) and Ireland (where less severe degradation is expected), hence adding data for these two countries would not alter the result substantially. Result is again strongly governed by Sweden, where half of the area is reported to be affected by moderate severity. As a results, data supports VU category, but note that degradation of this habitats still continues.

Criterion E Text:
There is no detailed modelling study for this habitat on European scale, even though literature suggests that there is a great risk of decline (Essl et al. 2012).

Synthesis:
The category Endangered (EN) is indicated by A1 and A3 categories describing declines in extent over respectively the last 50 years and a longer time frame. In addition, the total area (based on territorial data) is very low, as the habitat almost everywhere occurs in small stands. The subtypes that cover smaller areas and occur outside Sweden, Ireland and Estonia are even more threatened and if assessed separately, the Critically Endangered category should be expected. Considering still continuing and even accelerating degradation, loss of habitat specialists and bad restoration prospects reported by several regional studies, the resulting Endangered category has a high reliability.

Sub-habitats in Need of Examination:
The following subtypes deserve recognition: (1) Travertine fens, on active travertines in the intermountain basins of Western Carpathians of Slovakia with both fen specialists and subhalophytes, relicts of glacial times and extremely endanger

Contributors:
Habitat description: M. Chytrý
Territorial data: E. Agrillo, A. Alegro, S. Armiraglio, S. Assini, F. Attorre, L. Aunina, C. Bita-Nicolae, G. Buffa, L. Casella, A. ÄŒarni, R. Delarze, I. Diack, P. Dimopoulos, P. Finck, C. Giancola, D. Gigante, M. Hájek, B. Hamill, P. Ivanov, J. Janssen, P. Jones, N. Juvan, Z. KÄ…cki, G. Király, T. Kontula, E. Leibak, A. Lyngstad, V. Matevski, A. Mikolajczak, Ä. MilanoviÄ‡, A. Moen, J.A. Molina, B. Nygaard, F. O'Neill, D.I. Øien, J. Paal, D. Paternoster, G. Pezzi, V. RašomaviÄius, U. Raths, U. Riecken, D. Spray, A. Ssymank, J. Šibík, Å½. Škvorc, T. Tahvanainen, R. Venanzoni, P, Verté, D. Viciani, E. Weeda.
Help with data processing: E. Hettenbergerová
Working Group Mires & bogs: C. Bita-Nicolae, M. Hájek, F. Jansen, T. Tahvanainen


Habitat Type Name:
B3.1b Mediterranean and Black Sea rocky sea cliff and shore

Habitat Description:
This habitat type comprises open, halo-chasmophytic communities developing on the cliffs along the thermo-Atlantic, Mediterranean and Black Sea coasts. These coenoses develop under the influence of salt spray from the sea, especially in the supralittoral parts. Vertical to gently sloping bedrock and stable boulders in the supralittoral (or splash zone) of the majority of rocky shores are typically characterised by diverse maritime communities of yellow and grey lichens, such as Xanthoria parietina, Caloplaca marina, Lecanora atra and Ramalina spp. The black lichen Verrucaria maura is also present, but usually in lower abundance than in the littoral fringe zone. In wave exposed conditions, where the effects of salt spray extend further up the shore, the lichens generally form a wide and distinct band. The higher parts of sea cliffs are colonized by disjunct assemblages of salt-tolerant, halophytic or even halo-nitrophilous crevice plants (chasmophytes) or by more or less closed salt-tolerant grasslands (mainly on the cliff top). Perennial herbs are dominant, but also some annuals occur. There are processes of aridisation of the vegetation on the top of the higher rocks where the floristic composition is richer in different species depending upon the neighbouring dominant vegetation. The floristic composition depends also on the bedrock types, which are very diverse in the different part of habitat’s range. The main two groups are calcareous and silicate (often with volcanic origin) rocks and even loess-sand low cliffs along the Romanian Black Sea coast. Rare and endemic plants as well as widely distributed and ruderal nitrophilous species occur in the species composition. The vegetation belongs to the class Crithmo-Staticetea and the character species Crithmum maritimum is common everywhere in the habitat’s range. The Mediterranean sea cliffs harbour numerous endemics of extremely local occurrence, in particular many species belonging to the genus Limonium, which comprises at least 43 and probably 120 to 150 Mediterranean cliff species, many of which restricted to a few localities. Several of these species are seriously threatened, like for instance Limonium remotispiculum of southern Italy and Limonium strictissimum of Corsica and Caprera. Some stable and high coastal cliffs are inhabited by shrub communities of Ficus carica, Colutea arborescens and Ulmus minor.
Indicators of good quality:
In good conditions this habitat is rich in regional endemic species and the natural floristic structure is given by salt-tolerant chasmophytic species and halophytes. It is threatened by natural causes: the abrasive activities of sea waves leading to the natural destruction of the rocks. Other threats are the tourist development of the coastal areas, pollution and nitrification of the coastal cliffs and increase of not typical ruderal or alien species.
Characteristic species:
Flora
Vascular plants: Allium commutatum, Ameria ruscinonensis, Anthemis rigida, Anthyllis barba-jovis, Asteriscus maritimus, Atriplex hastata, Atriplex tatarica, Bellium crassifolium, Bellium minutum, Brassica insularis, Brassica tyrrhena, Catapodium marinum, Centaurea cineraria, Centaurea filiformis, Cephalaria mediterranea, Cichorium intybus, Cichorium spinosum, Crithmum maritimum, Convolvulus lineatus, Crucianella rupestris, Daucus carota, Daucus gingidium, Dianthus sardous, Ecballium elaterium, Elymus pycnanthus, Euphorbia pithyusa, Halimione verrucifera, Frankenia hirsuta, Frankenia laevis, Frankenia pulverulenta, Helichrysum litoreum, Helichrysum pseudolitoreum, Helichrysum rupestre, Hyoseris taurina, Genista tyrrhena, Goniolimon collinum, Kochia prostrata, Lactuca saligna, Leuzea salina, Limonium sp.pl., Lotus cytisoides, Melilotus officinalis, Parapholis incurva, Phleum crypsoides, Phleum exaratum, Phleum subulata, Plantago weldenii, Prangos ferulacea, Psilurus incurvus, Reichardia picroides, Sagina maritima, Scolymus hispanicus, Sedum litoreum, Senecio bicolor, Senecio cineraria, Seseli bocconii, Silene caliacrae, Silene compacta, Silene martinolii, Silene sedoides, Valantia muralis, Xanthium spinosum.
Lichens: Caloplaca marina, Lecanora atra, Ramalina sp.pl. Verrucaria maura, Xanthoria parietina 
Fauna
Invertebrates: Ligia italica, Littorina neritoides.
Birds: Apus apus, Calonectris diomedea, Falco eleonorae, Hydrobates pelagicus, Larus audouinii, Phalacrocorax aristotelis, Puffinus yelkouan, Sturnus roseus, Oenanthe pleshanca 
Mammals: Monachus monachus.

Classification:
EUNIS:
B3.1 Supralittoral rock (lichen or splash zone)
B3.2 Unvegetated rock cliffs, ledges, shores and islets
B3.3 Rock cliffs, ledges and shores, with angiosperms
Annex 1:
1240 Vegetated sea cliffs of the Mediterranean coasts with endemic Limonium spp.
EuroVegChecklist alliances:
Crithmo-Staticion Molinier 1934
Limonion anfracti-cancellati (Horvatic 1934) Mucina nom nov (=Staticion dalmaticum Horvatic 1934 )
Crithmo-Limonion graeci Géhu et al 92 (= Crithmo-Frankenion hirsutae Mayer 1995)
Kochio prostratae-Limonion meyeri Korzhenevsky 1987
Dactylido hispanicae-Helichrysion stoechadis Géhu et Biondi in Géhu 1984
Astragalion tragacanthae (Folch ex Rivas-Mart., Fernández-González et Loidi 1999) Rivas-Mart. et al. 2002
Launaeion cervicornis (O. de Bolòs et Vigo ex Gil et Llorens 1995) Rivas-Mart., Fernández-González et Loidi 1999
Euphorbion pithyusae Biondi et Géhu in Géhu et Biondi 1994
Anthyllidion barbae-jovis S. Brullo et De Marco 1989
Plantagini-Thymelaeion hirsutae Bartolo et S. Brullo in Bartolo et al. ex Mayer 1995
Crucianellion rupestris S. Brullo et Furnari 1990
Emerald:
B3.3 Rock cliffs, ledges and shores, with angiosperms                                                
MAES:
Coastal
IUCN:
13.1 Sea Cliffs and Rocky Offshore Islands

Justification Outstanding Example of Biogeographical Region:
Although this habitat is well represented in most of the EU28 countries, it is typical of the Mediterranean and Baltic regions.

Map Description:
Map is complete for EU28, but with data gaps for Croatia (where the habitat is widespread), Montenegro and Albania. Data sources: Art17, NAT.

Comment EU28+:
The provided quantitative data are not complete.

Trends in Quantity:
The trend in quantity is decreasing in almost all the countries of occurrence, especially those where the habitat is well represented (Italy, France, Croatia, Spain,, Greece), but in general decreases are relatively small.

Trends in Quality:
In most of the EU28 countries, the trend in quality is decreasing.

% of Distribution of the Habitat Type within the EU 28:
About 40 to 50% (estimation) of the habitat distribution lies within the EU28.

Justification of Small Range/Regression:
Although quantitatively declining, this habitat type has a huge range, as attested by its EOO larger than 50000 km2 and AOO larger than 50km2.

Justification of Restricted Area:
This habitat type has a huge range, as attested by its EOO larger than 50000 km2 and AOO larger than 50km2. It also occurs in large (linear) stands.

Pressures and Threats:
Several threats have been reported. The most significant ones are the increasing urbanisation and frequentation linked to tourism expansion.

Conservation and Management:
In protected areas, the fencing of degraded places and control of freqentation allow the natural regeneration of this habitat.

Conservation Status:
Annex I:
1240: MED U1, CON FV, BLS U1
Small parts are assigned under 1230

Capacity to Recover its Typical Character and Functionality?:
The recovery process of degraded areas is quite rapid if the frequantation is organised and controled.

Summary:
This habitat occurs as linear, narrow and often broken stretches of vegetated crevices, ledges and cliff-tops along the coasts of the Mediterranean and Atlantic round to mid-Portugal, and more locally, the Black Sea. Exposed bedrock dominates the habitat and its variable composition and structure determines the character of available surfaces, the height and slope of the cliffs influencing the input of salt spray which, on exposed coasts, can be very high close to the sea.  This combination of local climatic and topographic conditions determines the often strong zonation of crevice vegetation and grasslands found on the cliffs, with regional climate also affecting the flora, with many endemics characterising the Mediterranean element. It is threatened by natural erosion and also by recreation and urbanisation. No specific conservation measures are needed, except on frequently visited and degraded areas, where coastal restoration programmes can limit access and damage.

References:
Bartolo G., Brullo S. & Signorello P., 1989. La classe Crithmo-Limonietea nella penisola italiana. Coll. Phytosoc. 19: 55-81.
Crespo M.B., De la Torre A. & Costa M., 2003. Las comunidades de Crithmo-Staticion Molinier 1934 (clase Crithmo-Staticetea Br.-Bl. in Br.-Bl., Roussine & Nègre 1952) en la Península Ibérica e Islas Baleares. Phytocoenologia 33: 527–559.
Van der Maarel E., Van der Maarel-Versluys M., 1996. Distribution and conservation status of littoral vascular plant species along the European coasts. Journal of Coastal Conservation 2: 73-92.
Géhu J.M. & Biondi E., 1994. Végétation du littoral de la Corse: essai de synthèse phytosociologique. Braun-Blanquetia 13:1-149.

Criterion A Text:
Over the last 50 years, the overall reduction in quantity is slight (-9%), based on the EU28 countries of occurrence. The quantitative values for applying Criterion A1 are calculated from territorial data provided by 10 EU28 countries, including those with the largest areas. For A2 and A3, there is no possibility to evaluate since the provided data are incomplete. No quantitative data are available for EU28+ countries. The application of Criterion A1 leads to Least Concern status.

Criterion B Text:
This habitat is widespread in 11 EU28 and 3 EU28+ countries; the values of its EOO and AOO are far too large to meet the thresholds for the threatened categories under Criterion B. For these reasons, based on its geographic distribution, the habitat is assessd as Least Concern.

Criterion C/D Text:
Values have been calculated from territorial data provided by 10 EU28 countries, including the countries with the largest areas. Several countries reported a slight to moderate decrease in quality (the highest values were recorded in Portugal, Bulgaria and Italy), in some others the qualitative trend is more or less stable (e.g. Greece, Slovenia, Romania). Over the last 50 years, the overall reduction in abiotic/biotic quality was rather low (-22%), affecting a very small extent (4%). No data were available for additional EU28+ countries. Based on the application of Criterion C/D1, the habitat is assessed as Least Concern.

Synthesis:
All provided data lead to the conclusion that the habitat qualifies as Least Concern (LC) because the negative trends in quantity and in quality are small, and the habitats has a wide geographical distribution.

Sub-habitats in Need of Examination:
A Black Sea versus a Mediterranean sub-type can be considered, due to biogeographic, floristic and ecological differences. Salinity and salt spray exposure are lower in the Black Sea than in the Mediterranean, and the Mediterranean subtype contains muc

Contributors:
Habitat Definition: R. Tzonev
Territorial data : A. Acosta, O. Argagnon F. Bioret, J.Capelo, A. ÄŒarni, P. Dimopoulos, D. Espírito-Santo, M. Fagaras, C. Gussev, Juvan, J. Loidi, C. Marcenò, D. MilanoviÄ‡, I. Prisco, Škvorc
Working Group Coastal : A. Acosta, F. Bioret, H. Gardfjell, J. Janssen, J. Loidi, R. Tzonev


Habitat Type Name:
A5.23 Faunal communities in Mediterranean infralittoral fine sand

Habitat Description:
This habitat is formed on clean sands of shallow waters (between 4 and 25 m depth) on open coasts, subjected to moderate wave action, which allows for the accumulation of organic matter and fine sediments (<63 µm). These bottoms are dominated by deposit feeders, but filter feeders and carnivores are also present. Invertebrate assemblages found in this habitat correspond to those described as 'Littoral Fine Sand assemblages' (dominated by Spisula subtruncata), but are very close to muddy assemblages (Littoral Sandy Mud and Terrigenous Coastal Mud). Although this habitat typically lacks a significant seaweed or seagrass component, the presence of Cymodocea nodosa or Posidonia oceanica is frequent.
Several sub-habitats have been described. These are a sub-habitat of Spisula subtruncata, characterized by the bivalves Spisula subtruncata and Lucinella divaricate; a sub-habitat of Nephthys hombergii which is a transitional assemblage to circalittoral habitats;and a sub-habitat with Lentidium mediterraneum which is commonly associated to sandy flat areas shallower than 4 m depth, in estuaries and embayments.
Indicators of quality:
Most of the species included in the description of the habitat are bioindicators of environmental quality. The majority of bivalves are very sensitive to eutrophication and population changes in abundance and composition might indicate a change on habitat quality.
 
Characteristic species:
Molluscs: Spisula subtruncata, Lucinella divaricata, Donax trunculus, Tellina fabula, Thracia papyracea, Dosinia lupinus, Loripes lucinalis, Lentidium mediterraneum, Corbula gibba, Cerastoderma glaucum, Tellina tenuis. 
Crustacea: Apseudopsis latreillii, Siphonoecetes dellavallei, Lembos sp., Bathypoeia guillamsoniana, Ampelisca brevicornis, Perioculoides longimanus, Urothoe intermedia, Pseudocuma longicorne, Ampelisca diadema, Diogenes pugilator, Portumnus latipes. 
Fish: Gymnammodytes cicerelus, Arnoglossus laterna, Xyrichtys novacula.
Annelida: Owenia fusiformis, Paradoneis armata, Spio decoratus, Prionospio caspersi, Mediomastus fragilis, Magelona mirabilis, Peresiella clymenoides, Ditrupa arietina, Notomastus aberans, Chone duneri, Nephthys hombergii, Aponuphis bilineata, Scolelepis squamata, Scoletoma impatiens, Lumbrineris latreilli, Spiochaetopterus costarum.
Sipunculida: Aspidosiphon sp.
Echinodermata: Spatangus purpureus, Echinocardium mediterraneum. 
Nematoda: different species.

Classification:
EUNIS (v1405):
Level 4: A sub-habitat of A5.23 Infralittoral fine sand
 
Annex 1:
1110 Sandbanks slightly covered by sea water all time
1160 Large shallow inlets and bays 
 
MAES
Marine - Marine inlets and transitional waters
Marine - Coastal
 
MSFD:
Shallow Sublittoral Sand
 
EUSeaMap:
Shallow sands
 
IUCN: 
9.4. Subtidal sandy  
9.5. Subtidal Sandy-mud

Map Description:
This map has been generated using data based IUCN based on EMODNet Database. EOO and AOO have been calculated on the available data presented in this map however these should be treated with caution as expert opinion is that this may not indicate the full distribution of the habitat.

Trends in Quantity:
This habitat is common along the Mediterranean shores. Although no detailed information exists for the south and eastern Mediterranean, it is known to be widely distributed. Research and long-term monitoring data are available only for a few localities (e.g. Gulf of Lion). There are no reports about the trends on this habitat from individual countries and specific information regarding the trends of the different sub-habitats is missing. Therefore, the average current trend in quantity at the EU 28 and the EU 28+ levels is unknown.

Trends in Quality:
Long-term data series from monitoring of this habitat are scarce. In Banyuls-sur-Mer (northwestern Mediterranean Sea), temporal changes in macrofaunal composition between 1967–1968, 1994 and 2003 have been observed (i.e. increase of the polychaete Ditrupa arietina within the Spisula subtruncata and Nephtys hombergii communities, and the decrease of the polychaetes Scoloplos armiger and Notomastus latericeus in the S. armiger community). Similarly, in the Gulf of Lion, influenced by the Rhône River, major changes in the composition of the benthic macrofauna forming this habitat have also been observed (e.g. dramatic increase of the serpulid polychaete Ditrupa arietina). In Greece, no trends can be determined due to the patchiness of data and lack of continuous long-term data. In addition, sites that are monitored here are usually located at areas ifluenced by anthropogenic impacts. Therefore, the average current trend in quality remains unknown.

% of Distribution of the Habitat Type within the EU 28:
Limited information on this habitat type is available, and much of its current distribution in the eastern Mediterranean is unknown or unavailable, although it is known to be widespread throughout the Mediterranean Sea. An estimation of its percentage distribution within the EU 28 is unavailable until more accurate estimates of its distribution are provided.

Justification of Small Range/Regression:
Tha habitat has an EOO larger than 50,000 km2.

Justification of Restricted Area:
The habitat is widespread along the Mediterranean coast and EOO is larger than 50,000 km2.

Pressures and Threats:
The habitat is directly affected by various anthropogenic impacts resulting from urban, industrial, agricultural, aquaculture and other coastal activities. Fishing and aggregate dredging activities can also alter the composition of the biological communities and its productivity.
Fishing may affect the physical integrity of the sediment system whilst dredging activities, spoil disposal and aggregate extraction would affect the sediment and hydrographic regime through a variety of effects. Other disturbances to the species (e.g. litter, extraction of species, species introduction) should also be considered.

Conservation and Management:
There are no current specific conservation actions in place for this habitat. The broad distribution of this habitat makes it likely to occur in protected areas, however detailed information is missing. A wide survey to assess the distribution of this habitat is needed in order to better evaluate its conservation and management. The designation of reference sites for long monitoring trends and the continuation of those already existing will assist to examine the trends in this habitat.
Moreover, improving spatial and strategic planning of human activities, in particular to promote the wiser use of habitats where there are competing demands (e.g. fishing, sand and gravel extraction) is necessary in order to ensure the good conservation status of this habitat in the Mediterranean Sea.

Conservation Status:
Annex 1:
1110: MMED XX 
1160: MMED XX
This habitat is listed as an endangered natural habitat type in the Resolution no. 4 (Council of Bern Convention, 1996): Sublittoral soft seabeds (code 11.22).

Capacity to Recover its Typical Character and Functionality?:
In high-energy environments where this habitat occurs, the impact of human activities may be considered transitory and negligible and therefore recovery might be relatively fast.

Summary:
Infralittoral fine sands in the Mediterranean play a substantial role in maintaining the balance of sandy beaches. Its epifauna and infauna may be rich and diverse, and the habitat supports some commercial species, such as shellfish. Organic enrichment from natural and anthropogenic sources is a common pressure to this environment that can lead to a change in the species assemblage. Physical damage (sediment extraction, siltation) resulting from fishing practices, dredging to remove aggregates and introduction or spread of non-indigenous species can also affect the habitat.
There are few studies on the characterization of infralittoral communities in these soft bottom Mediterranean environments and information regarding the trends and condition of this habitat are scarce. There are no current specific conservation actions in place for this habitat. The broad distribution of this habitat makes it likely to occur in protected areas. The designation of reference sites for long monitoring trends and the continuation of those already existing will assist to examine the trends in this habitat. Moreover, improving spatial and strategic planning of human activities, in particular to promote the wiser use of habitats where there are competing demands (e.g. fishing, sand and gravel extraction) is necessary in order to ensure the good conservation status of this habitat in the Mediterranean Sea.

References:
Bakalem, A., Ruellet, T. and Dauvin, J.C. 2009. Benthic indices and ecological quality of shallow Algeria fine sand community. Ecological Indicators 9: 395-408.
Bertasi, F., Colangelo, M.A., Colosio, F., Gregorio, G., Abbiati, M. and Ceccherelli, V.U. 2009. Comparing efficacy of different taxonomic resolutions and surrogates in detecting changes in soft bottom assemblages due to coastal defence structures. Marine Pollution Bulletin 58: 686-694.
Desbruyères, D., Guille, A. and Ramos, J. 1972-73. Bionomie benthique du plateau continental de la côte catalane espagnole. Vie Milieu 23: 335-363.
Elliot, M., Nedwell, S., Jones, N.V., Read, S.J., Cutts, N.D. and Hemingway, K.L. 1998. Intertidal sand and mudflats & subtidal mobile sandbanks. In: An overview of dynamic and sensitivity for conservation management of marine SACs. Scottish Association for Marine Science for the UK Marine SACs Project.
Gambi, M.C. and Giangrande, A. 1986. Distribution of soft-bottom polychaetes in two coastal areas of the Thyrrenian Sea (Italy): structural analysis. Estuarine, Coastal and Shelf Science 23: 847-862.
Grémare, A., Sardá, R., Medernach, L., Jordana, E., Pinedo, S., Amouroux, J.M., Martin, D., Nozais, C. and Charles, F. 1998. On the dramatic increase of Ditrupa arietina. O.F. Müller (Annelida: Polychaeta) along both the French and the Spanish catalan coasts. Estuarine, Coastal and Shelf Science 47: 447-457.
Guille, A. 1970. Bionomie benthique du plateau continental de la côte catalane française. II. Les communautés de la macrofaune. Vie Milieu 1B: 149-280.
Guille, A. 1971. Bionomie benthique du plateau continental de la côte catalane française. IV. Densités, biomasses et variations saisonnières de la macrofaune. Vie Milieu 22: 93-158.
Labrune, C., Grémare, A., Amouroux, J.-M., Sardá, R., Gil, J. and Taboada, S. 2007. Assessment of soft-bottom polychaete assemblages in the Gulf of Lions (NW Mediterranean) based on a mesoscale survey. Estuarine, Coastal and Shelf Science 71: 133-147.
Labrune, A. Grémare, Guizien, K. and Amouroux, J.M. 2007. Long-term comparison of soft bottom macrobenthos in the Bay of Banyuls-sur-Mer (north-western Mediterranean Sea): A reappraisal. Journal of Sea Research 58, 125–143.
Massé, H. 1972. Quantitative investigations of sand-bottom macrofauna along the Mediterranean north-west coast. Marine Biology 15: 209-220.
Occhipinti-Ambrogi, A., Favruzzo, M. and Savini, D. 2002. Multi-annual variations of macrobenthos along the Emilia-Rogmana coast (Northern Adriatic). Marine Ecology 23: 307-319.
Pinedo, S., Sardá, R. and Martín, D. 1992. Seasonal dynamics and structure of soft-bottom assemblages in Blanes Bay (northwest Mediterranean Sea). Publicaciones Especiales del Instituto Español de Oceanografía 22: 61-70.
Salen-Picard, C. and Arlhac, D. 2002. Long-term Changes in a Mediterranean Benthic Community: Relationshhips Between the Polychaete Assemblages and Hydrological Variations of the Rhône River. Estuaries 25: 1121–1130.
Sardá, R., Pinedo, S. and Martin, D. 1999. Seasonal dynamics of macroinfaunal key species inhabiting shallow soft-bottoms in the Bay of Blanes (NW Mediterranean). Acta Oecologica 20: 315-326.
Sardá, R., Serrano, L., Labrune, C., Gil, J., March, D., Amouroux, J.-M., Taboada, S., Bonifàcio, P. and Grémare, A. 2014. Shallow water polychaete assemblages in the northwestern Mediterranean Sea and its possible use in the evaluation of good environmental state. Memoirs of Museum Victoria 71: 289-301.

Criterion A Text:
There is a lack of information on trends in quantity of this habitat in most countries where it occurs. It has therefore been assessed as Data Deficient under Criterion A for both the EU 28 and EU 28+.

Criterion B Text:
The habitat has a patchy distribution in the Mediterranean Sea, but it is estimated that both the EOO and the AOO exceed the thresholds for a threatened Category. There is no information available on whether there is a continuing decline in the spatial extent or the biotic and abiotic quality and on whether a threatening process will likely cause continuing declines. This habitat has therefore been assessed as Least Concern under Criterion B1 and B2 and Data Deficient for all other criteria for both the EU 28 and EU 28+.

Criterion C/D Text:
The current trend regarding the biotic and abiotic quality of the habitat is unknown as little research and monitoring has been conducted on it. Nonetheless if pressures stop, the habitat might recover naturally. In France, a decrease on the biotic quality of the habitat has been reported but for most of the EU 28 and EU 28+ the information is unknown. Based on this, the habitat type is assessed as Data Deficient under Criteria C/D.

Synthesis:
This is a widespread habitat in the Mediterranean Sea, however there is very little information on its distribution, impacts and reductions in quantity and quality. The habitat has a large Extent of Occurrence (EOO) and Area of Occupancy (AOO), and therefore qualifies as Least Concern under Criterion B. However, the habitat is assessed as Data Deficient for both the EU 28 and the EU 28+ because of a lack of information on its trends in quantity and quality.


Habitat Description:
Springs are habitats where groundwater discharges to earth surface or to a water body. Their microclimate, hydrology, water volume, chemistry and discharge type (rheocrene, limnocrene, and helocrene springs), and consequently animal and plant communities, are very variable. Sometimes springs are dominated by abiotic features, sometimes their biotic communities are very rich (particularly helochrenes with moss carpets, specialized plants and macroinvertebrates). Springs are usually small-sized but in some cases large complexes (up to several hectares) of pools, vegetation patches and moist seepage areas occur. As compared to other moist habitats spring habitats are characterized by low temperature, small annual fluctuation in the water temperature, and often by high content of oxygen in the water. These features are most representative in cold stenothermic springs where mean temperature is only a few degrees above 00C and the annual amplitude is very small. The pH of base-poor springs is typically from slightly acid, form pH > 5.5 to circumneutral or slightly alkaline. The diverse physical structure and the water chemistry are main determinants for spring biota, the former particularly to macroinvertebrates, the latter to bryophytes. Through groundwater, rich in nutrients and oxygen, springs have often locally enriching influence to adjacent habitats, for example to headwater streams or to mire, meadow or forest habitats. On the other hand, adjacent habitats, for example forest, can have strong influence on springs and spring brooks, both by shadowing and as a source of allochthonous material. The stenothermic springs in cold (arctic, alpine) areas are dominated by mosses, while cover of vascular plants (such as Saxifraga spp., Koenigia islandica, Epilobium hornemanni) is low or zero. In montane and subalpine springs vascular plants, representing alpine and arctic floristic elements, are more common, but in most cases moss communities prevail. In lowland springs vascular plants can be abundant. Due to their characteristic microclimate, with a low temperature during the growing season, springs can accommodate disjunct (often relict) occurrences of northern and alpine species. However, in northern locations, they can maintain also occurrences of species with southern origin, due to unfrozen water and soil during wintertime. Spring habitats are sensitive to disturbances, because they are affected by changes in their close surroundings but also in their catchment areas. Many springs have been destroyed or deteriorated in quality due to a range of activities related to groundwater abstraction, utilisation of spring brooks, forestry, clearing of agricultural land, soil and rock excavation, and construction activities. Threats include eutrophication and chemical contamination too. In arctic, alpine and north boreal areas spring habitats have remained to large extent in natural condition, in lowlands many of them have been destroyed or their quality declined.
Indicators of good quality:
Natural hydrology and water chemistry in springs and spring brooks,
Low anthropogenic influence (drainage, water exploitation, forestry, agriculture, eutrophication etc.) in springs, their surroundings and catchment areas,
Presence of plants and animals adapted to spring conditions, including threatened species,
High cover of mosses and specialized vascular plants,
Rich macro-invertebrate fauna,
Low cover of encroaching tall grasses and shrubs.
Absence of invasive alien species.

Characteristic species:
Flora: Vascular plants: Cardamine amara, Montia fontana, Epilobium alsinifolium, E. nutans, E. hornemannii, E. obscurum, E. palustre, Carex acutiformis, C. paniculata, C.remota, C. vaginata, Cardamine flexuosa, Chrysosplenium alterniflorum, C. oppositifolium, Circea alpina, C. x intermedia, Crepis paludosa, Impatiens noli-tangere, Myosotis stolonifera, Petasites frigidus, Poa remota, Saxifraga aizoides, Saxifraga stellaris, Stellaria alsine, Veronica nevadensis.
Mosses: Brachythecium rivulare, Bryum weigelii, Bryum schleicheri, Calliergon cordifolium, Chiloscyphus polyanthos, Cratoneuron filicinum, Mniobryum, Philonotis fontana, Philonotis tomentella, Pohlia wahlenbergii, Rhizomnium, Plagiomnium, Scapania uliginosa, Scapania undulata, Sphagnum riparium, Sphagnum squarrosum, Sphagnum teres, Warnstorfia exannulata.
Fauna: Birds: Cinclus cinclus.
Invertebrates: Plecoptera,Trichoptera, Diptera (Chironomidae,Simulidae), Gammarus spp., Asellus aquaticus, Pallasea quadrispinosa, Cladocera.

Classification:
EUNIS:
C2.1. Springs, spring brooks and geysirs
EuroVegChecklist (alliances):
Caricion remotae Kästner 1941
Cratoneuro filicini-Calthion latae Hadac 1983
Mniobryo-Epilobion hornemannii Nordhagen 1943
Koenigio-Microjuncion Sörensen ex Hadac 1971
Cardamino-Montion Br.-Bl. 1926
Swertio perennis-Anisothecion squarrosi Hadac 1983
Epilobio nutantis-Montion Zechmeister in Zechmeister et Mucina 1994
Myosotidion stoloniferae Rivas-Martinez et al. 1984
Pinguiculo balcanicae-Cardaminion acris Carni et Matevski 2010
Ranunculion omiophyllo-hederacei Rivas-Martinez et al. 2002
Annex 1:
7160 Fennoscandian mineral-rich springs and springfens
Emerald:
C2.111 Fennoscandian mineral-rich springs and springfens
MAES-2:
Freshwater, Rivers and lakes
IUCN:
5.9. Freshwater Springs and Oases

Justification Outstanding Example of Biogeographical Region:
The habitat is very widespread in Europe. Although it is best conserved in alpine regions, it is also occurring in lowland areas.

Map Description:
Map is incomplete. Data gaps exist amongst others in Italy, France, the Carpathians and on the Balkan. Data sources: EVA, GBIF.

Comment EU28:
Sites numerous, but usually small in size

Comment EU28+:
Sites numerous, but usually small in size

Trends in Quantity:
Springs and spring brooks have severely declined in many countries, particularly in lowlands, due to water abstraction, land reclamation and pollution. However, this has been documented in detail only in a few countries. Declining trend of natural spring habitats is clear during the last 50 years. This trend is supposed to continue also in the future. Current total area of the habitat is difficult to estimate, as sites are numerous but often very small in size, and the methods used in inventories varies between the countries. Total area may be 200 - 300 km2 in EU28.

Trends in Quality:
The quality of springs and spring brooks has declined in most countries (declining trend in 13 of 17 countries in analyses) during the last 50 years. In most countries severity of degradation has been estimated to be moderate or severe.

% of Distribution of the Habitat Type within the EU 28:
Based on total distribution of some characteristic species (Montia fontana, Cardamine amara, Epilobium alsinifolium) about 60 % of base-poor springs and spring brooks with this type of vegetation lies within EU28.

Justification of Restricted Area:
Springs and spring brooks have a wide European range, but their total area is limited due to scattered occurrence of sites, all with small areas. This and a considerable regional and local variation make their communities sensitive to many kinds of cha

Pressures and Threats:
As small-scale habitats springs and spring brooks are very sensitive to various changes in their surroundings, as well as in their catchment areas. During last centuries they have been subjected to water abstraction, changes in the hydrology, land reclamation and many types of pollution. These pressures have caused decline in the quantity of springs, as well as losses in their biota. Losses in plant and animal communities are often much more severe than changes in abiotic conditions, for example groundwater volume. Consequently, springs were largely lost in many European lowland areas. In recent past hydrological changes have continued, as well as input of nutrients. Diffuse loading of nutrients from agriculture and forestry, and air-borne pollution, particularly nitrogen, is more common than earlier. Hydrological changes and increasing nutrient loads result in successions to more productive plant communties and overgrowth by taller plants. In future climate change is evidently going to enhance this trend. Recreation activities as well as soil excavation (sand, gravel, peat) can be locally important. In general, springs in lowland and southern regions are much more impacted by these pressures than springs in northern and alpine areas. Spring habitats and many spring species are qualified threatened in many national red lists.

Conservation and Management:
Maintaining natural hydrology and controlling eutrophication and contamination are main approaches in conservation of springs and their surroundings. Water protection measures are needed also in catchment areas. Springs and spring brooks are often small-size habitats (often from a few to some tens of m2), therefore their vegetation and fauna is sensitive to many kinds of changes. They should be taken into consideration when running agricultural and forestry practices. Representative spring sites should be legally protected. Sometimes it is necessary to develop specific management and restoration schemes to spring biota.

Capacity to Recover its Typical Character and Functionality?:
In many cases the habitat has some capacity to recover, but in most cases interventions related to restoration of hydrology, decreasing nutrient loads and other type of pollution are required. Often spring vegetation and fauna require specific restoration measures. Various restrictions in land use and recreation activities are often needed in close surroundings. The habitat may be restored within a relatively short period, but for some of the biota it may take many decennia to return to the habitat, because of isolated populations and limited dispersal potential.

Summary:
Base-poor springs and spring brooks develop throughout Europe where ground water emerges from bedrock or superficial deposits and are usually small in size but can occur in extensive complexes. The speed, volume and chemistry of the waters are very variable and the associated flora and fauna accordingly diverse. Moss carpets often prevail among the vegetation cover, though distinctive vascular plants occur in less extreme situations, including some relic species. Very sensitive to disturbance, they are threatened by water abstraction, quarrying and mining, land clearance and construction. Restoration depends on recovering the natural hydrology.

References:
Ilmonen, J. 2009. Benthic macroinvertebrate and bryophyte assemblages in boreal springs: diversity, spatial patterns and conservation. Acta Universitatis Ouluensis. A 523, 52 pp.
Leka, J. et al. 2008. Sisävedet ja rannat [Inland waters]. In Raunio, A., Schulman, A. & Kontula, T. (eds.), Suomen luontotyyppien uhanalaisuus [Assessment of threatened habitat types in Finland]. Osa 2. Luontotyyppien kuvaukset [Part 2. Habitat type descriptions]. Suomen Ympäristö / The Finnish Environment 8/2008: 89-142.
Lindgaard, A. & Henriksen, S. (eds.) 2011. The 2011 Norwegian Red List for Ecosystems and Habitat Types. Norwegian Biodiversity Information Centre. Trondheim. 122 pp.
Molina, J.A. 2001. Oligotrophic spring vegetation in Spanish mountain ranges. Folia Geobotanica 36: 281-291.
Påhlsson, L. (ed.)1994. Vegetationstyper I Norden. TemaNord 1994: 665, 626 pp. Nordic Council of Ministers, Copenhagen.

Criterion A Text:
Reduction in quantity in the recent past (Criterion A1) is calculated from quantitative data from 14 EU28 countries. In many cases data derived from expert judgment. There are quantitative estimates from only few countries on area of base-poor spring habitats in last centuries or in future. So no assessment could be done for criteria A2a, A2b and A3. The average decline of -20% leads to a Least Concern (LC) assessment.

Criterion B Text:
The EOO and AOO of the habitat are much larger than the thresholds for criterion B.

Criterion C/D Text:
Data from 18 countries (16 from EU28) were available. Quantitative estimates of the extent of degraded areas were made from 13 countries (12 decrease, 1 stable, 5 unknown) and of the severity of the degradation from 14 countries (13 decrease, 1 stable, 4 unknown). Data combining extent and severity of degradation were, however, only  available from 6 EU28 and 2 EU28+ countries. The data represents in many countries expert judgment and data coming from the WPD and Article 17 reporting, and is - compared to many other habitats - rather uncertain. In these reporting abiotic and biotic parameters are often combined to give an overall estimate.
Because of the uncertainty in data and data gaps several different calculations have been carried out, using assumptions about amount and trends of the habitat in countries with data gaps. This resulted in a degraded extent of the habitat of about 45 to 55 %, and a severity of about 45 to 65 %, both for EU28 and EU28+. With these figures the habitat is assessed as Vulnerable (VU) under criterion C/D1 for the EU28. For the EU28+, however, important data from Norway and Iceland is lacking, two countries where the habitat is widely distributed. It is assumed that the habitat in these countries is relatively well preserved. Therefore for the EU28+ the category NT is concluded.

Synthesis:
The area of the habitat has decreased in most countries, on average about 20% in Europe. The remaining area suffered a strong decline in quality (severity 45-65%, affected area 45-55%), resulting in the category Vulnerable (VU) for EU28. Data from EU28+ covered two additional countries, leading to similar trends. However, base-poor springs are widespread in Iceland and Norway, countries from which no data were available, and it is likely that the habitat is in a relatively good status there. As information from these countries is likely to decrease trend values, the lower category Near Threatened (NT) is applied for EU28+.

Sub-habitats in Need of Examination:
Lowland and alpine base-poor springs and spring brooks differ in biota, pressures and conservation status. Lowland base-poor springs are likely to have a much higher degree of threatening than the alpine sub-habitat. Geysirs are a specific sub-habitat

Contributors:
Type description: H. Toivonen
Territorial data: S. Armiraglio, G. Arts, S. Assini, ABG Averis, AM Averis, J. Brophy, G. Buffa, J. Capelo, A. Carni, J-M. Couvreur, R. Delarze, L. Denys, D. Espírito-Santo, P. Finck, P. Ivanov, N Juvan, T. Kontula, M. Koci, A. Mikolajczak, J.A. Molina, D. Paelinckx, D. Paternoster, V. Rasomavicius, U. Raths, U. Riecken, Z. Skvorc, A. Ssymank, V. Stupar
Working Group Freshwater habitats: G. Arts, F. Landucci, J.A. Molina, B. Poulin, H. Toivonen


Habitat Type Name:
C2.2a Permanent non-tidal, fast, turbulent watercourse of montane to alpine regions with mosses

Habitat Description:
This habitat type includes small, shallow, fast-running and turbulent streams of montane and alpine regions of Europe. The water is highly oxygenated and rather cold during all seasons with temperatures rarely higher than 10°C in summer. The sediments consist almost exclusively of rocks and boulders, because the fast current does not allow the deposition of finer sediments. Vascular plants can occasionally occur in this habitat, especially in those parts of the riverbed where the current is slower and there is temporary accumulation of finer sediments. However no stable vascular plant community can be considered typical of this habitat type. Therefore the habitat does not include any vascular plant alliances, instead, lichens and bryophyte communities with high moss abundance are very characteristic of this habitat. The lichen and bryophytic vegetation is usually rather low in species number, on the contrary the fauna can be very rich including mainly stenothermic species of rheophile fauna.
Indicators of good quality:
Occurrence of stenothermic and rheophile fauna
High water velocity
Thin layer of algae covering the rocks, a thick layer of algae could be symptom of eutrophication in place
Absence of fine and organic sediments
Dominance of aquatic lichens and mosses
Natural hydrology

Characteristic species:
Algae: Phormidium autumnale, Cladophora spp., Hydrurus foetidus, Bangia atropurpurea, Diatoma spp., Gomphonema olivaceum, Melosira varians, Chamaesiphon polonicus, C. amethystinus, Tolypothrix distorta, Navicula spp., Nitzschia spp., Cocconeis spp., Spirogyra spp., Mougeotia spp., Zygnema spp., Oocardium stratum, Vaucheria spp., Hildenbrandia rivularis, Lemanea fluviatilis, Audouinella hermannii, Heribaudiella fluviatilis, Surirella ovata, Closterium leibleinii, Staurastrum punctulatum.
Lichens: Verrucaria spp., Porina clorotica, Dermatocarpon luridum
Bryophytes: Scapania undulata, Cratoneuron spp., Blindia acuta, Brachythecium rivulare, B. plumosum, Bryum spp., Dichodontium pellucidum, Fontinalis antipyretica, Hydrogrimmia mollis, Hygrohypnum molle, H. smithii, Jungermannia exsertifolia, Schistidium rivulare, Cinclidotus fontinaloides, C. riparius, Philonotis fontana, Pohlia wahlenbergii, Rhacomitrium fasciculare, Platyhypnidium riparioides.
Macroinvertebrates: Mollusca (e.g. Ancylus fluviatilis), Turbellaria, Crustacea (Cyclops spp., Attheyella spp., Bryocamptus spp., Maraenobiotus spp., Hypocamptus spp., Moraria spp., Parastenocaris spp., Potamocypris spp., Cavernocypris spp., Cryptocandona spp.), Ephemeroptera (e.g. Baetis alpinus, B. lutheri, B. melanonyx), Trichopetera (e.g. Hydropsyche instabilis, Potamophylax cingulatus, Rhyacophila spp., Sericostoma pedemontanum), Ephemeroptera (e.g. Epeorus alpicola, E. sylvicola, Rhithrogena loyolaea, R. alpestris, Ecdyonurus alpinus, Oligoneuriella rhenana), Odonata (e.g. Baetis alpinus, B. rhodani, Calopteryx splendens, C. virgo, C. haemorrhoidalis), Plecoptera (e.g. Dictyogenus fontium, Protonemura ausonia, P. caprai, P elisabethae, P. brevistyla, Nemoura mortoni, N. obtuse, Leuctra rosinae, L. festai, L. teriolensis, Isoperla rivulorum, Perlodes intricatus, Siphonoperla montana, Chloroperla susemicheli), Diptera (e.g. Diamesa spp., Chironomus spp., Orthocladius spp., Eukiefferiella spp., Tvetenia calvescens, Prosimulium spp., Simulium spp., Dicranota spp., Rhypholophus spp., Tricyphona spp., Thaumalea spp.)
Vertebrates: Fish: Salmo trutta, Cottus gobio, Thymallus thymallus; Birds: Cinclus cinclus

Classification:
EUNIS:
C2.2 Permanent non-tidal, fast, turbulent watercourses
EuroVegChecklist:
Scapanion undulatae Philippi 56
Dermatocarpion rivulorum Geissler 76 
Fontinalion antipyreticae W. Koch 1936
Rhynchostegion riparioides Waldh. 1944
Platyhypnidion rusciformis Philippi 1956
Annex 1:
3220 Alpine rivers and the herbaceous vegetation along their banks
32A0 Tufa cascades of karstic rivers of the Dinaric Alps
Possibly there is also some overlap with 3230 (Alpine rivers and their ligneous vegetation with Myricaria germanica) and 3240 (Alpine rivers and their ligneous vegetation with Salix eleagnos)
Emerald:
C2.18 Acid oligotrophic vegetation of spring brooks
MAES-2:
Freshwater habitat, rivers and lakes, inland surface water (water courses and bodies)
IUCN:
5.1. Permanent Rivers/Streams/Creeks [includes waterfalls]
Water Framework Directive:
R-E4 (Upland streams)

Justification Outstanding Example of Biogeographical Region:
The habitat is characteristic of montane to alpine regions across whole of Europe.

Map Description:
Map is incomplete, with main data gaps in the Alps, Carpathians and Balkan, but rather complete distribution for Bulgaria. Data sources: EVA, GBIF, NAT.

Comment EU28:
This is the area in 6 out of 12 countries

Comment EU28+:
This is the area in 7 out of 12 countries

Trends in Quantity:
The trends in quantity vary among the 13 countries for which territorial data are availablehave been submitted. In 8 countries the trend is decreasing, and in 3 countries the trend is stable and in 2. For two countries the trend is unknown. However most countries did not reported data about the current area of habitat, therefore an estimation of the trend in quantity at European scale was not possible.

Trends in Quality:
Ten countries (43% of the total countries in which the habitat is expected to occur) reported data about the trend in quantity, consisting of slight to severe degradation of at least 5 to up 70% of the habitat extent. However only 5 countries (only 20% of the total countries in which the habitat is expected to occur) reported the current area of habitat, therefore an estimation of the trend in quality at European scale was not possible.

% of Distribution of the Habitat Type within the EU 28:
This habitat type is widely distributed in the mountainous regions of Europe and Asia. Similar habitat types, but characterized by partially or totally different species, may be found across whole Northern hemisphere. Probably only 40% of the habitat in the Euro-Asiatic range lies within EU 28.

Justification of Small Range/Regression:
The habitat is widely distributed in mountainous and Alpine regions, so it has not a small natural range.

Justification of Restricted Area:
The habitat is widely distributed in mountainous and Alpine regions, so it has not a small natural range.

Pressures and Threats:
The habitat area has decreased due to construction of dams and water accumulation, construction of small power plants and water canalisation and riverbed modifications. Water pollution includes pollution from livestock, agriculture and households. A serious threat includes climate change, especially changes in temperature and precipitation that can alter the physical characteristics of the habitat.

Conservation and Management:
Current restoration measures consist of improving the hydrological regime and restoring water quality. Other measures needed for limiting the eutrophication may be regulating farming and agriculture in proximity of the streams and in the areas upstream. Institution of protected areas may be in some cases a good strategy for managing the land use.

Conservation Status:
Annex 1:
3220: ALP U1, ATL XX, BOR FV, CON U1, MAC FV, MED U1
32A0: no data reported yet

Capacity to Recover its Typical Character and Functionality?:
When the habitat is severely damaged, it takes a long time period to restore it. Restoring hydrology might not always be possible. Rises in temperature might not be overcome and might be deleterious to the stenothermic fauna.

Summary:
This habitat type includes small, shallow, fast and turbulent streams of montane and alpine regions of Europe with highly oxygenated and rather cold waters. The sediments consist almost exclusively of rocks and boulders and vascular plants are often confined to situations where the current is slower and there is temporary accumulation of finer sediments. Species-poor moss communities are the most usual feature but there can be a rich stenothermic fauna. Construction of dams and small power plants, water canalisation and riverbed modifications, pollution from livestock, agriculture and households are serious threats, together with climate change,  Restoration measures include the improvement of water quality and the recovery of the hydrological regime and a long time period is needed.

References:
Delarze, R. and Y. Gonseth, 2008. Guide des millieux naturels de Suisse. Rossolis, Bussigny. 424 pp.
Füreder, L. 1999. High alpine streams: Cold habitats for insect larvae, p. 181-196. In: Margesin, R. and Schinner, F. (eds.) Cold adapted organisms: Ecology, physiology, enzymology and molecular biology. Springer.
Minelli, A., Ruffo, S. and Stoch, F. (ed.) 2002. Torrenti montani. La vita nelle acque correnti. Quaderni Habitat 5. Ministero dell’Ambiente e della Tutela del Territorio e Museo Friuliano di Storia Naturale, Udine, 159 pp.
Ward, J.V. 1994. Ecology of alpine streams. Freshwater Biology 32: 277-294.

Criterion A Text:
Quantitative data for area are available for only 4 out of 14 countries reporting about this habitat. Therefore a quantiative assessment has been carried out without weighting for the area. The average trend (non-weighted) over the last 50 years is a decline of -16% (EU28) and -15% (EU28+) with maximum values reported from Austria (<50% decline) and Germany (30-50% decline), and stable situations in the UK, France and Finland.

Criterion B Text:
The habitat is presently largely extended in Europe therefore both EOO and AOO are far from the thresholds required by criterion B to consider the habitat threatened. However a decrease has been observed in spatial extent, biotic and abiotic quality. A future negative trend is expected due to climate change (rise of water temperature).

Criterion C/D Text:
Only 5 countries (about 20% of the total countries in which the habitat is expected to occur) reported all the data necessary to calculate the trend in quality (current area, extent of degraded area, trend in severity of degradation). Therefore the assessment according to criterion C and D have been considered not reliable at this moment. The habitat is Data Deficient according to this criterion.

Criterion E Text:
No data are available to evaluate risk of habitat collapse.

Synthesis:
A full quantitative assessment of the decline in abiotic and biotic quality and quantity was not possible for this habitat. Despite, the assessment according to criterion A1 (trends in quantity over 50 years) and criterion B (restricted geography) resulted to be Least Concern (LC), but the assessment has a relatively low certainty due to large data gaps.

Contributors:
Type description: G. Arts, F. Landucci, J.A. Molina, B. Poulin, H. Toivonen
Territorial data: S. Armiraglio, S. Assini, C. Bita-Nicolae, G. Buffa, A. ÄŒarni, R. Delarze, P. Finck, D. Gigante, P. Ivanov, N. Juvan, T. Kontula, C. Mainstone, A. Mikolajczak, J.A. Molina, D. Paternoster,  G. Pezzi, U. Raths, U. Riecken, Å½. Škvorc, A. Ssymank, V. Stupar, D. Viciani
Working Group Freshwater Habitats: G. Arts, F. Landucci, J.A. Molina, B. Poulin, H. Toivonen


Habitat Type Name:
H3.2d Mediterranean base-rich inland cliff

Habitat Description:
This habitat is composed of cliffs of limestone, calcareous conglomerates and other base-rich rocks in the Mediterranean, except if they are halophytic as a result of being under sea spray influence, with calcicole vascular plants, growing in fissures and crevices (chasmophytes), bryophytes, lichens and epi- and endolithic micro-organisms. The chasmophytic flora is diverse in composition and growth form; it consists mainly of perennial herbs, small ferns, dwarf shrubs, shrubs, tussock grasses, and sometimes woody climbers and small trees. Rosulate, prostrate, succulent and cushion are characteristic growth forms. Genera such as Asplenium, Campanula, Centaurea, Hieracium, Saxifraga, Silene and Teucrium are particularly species-rich and well represented in many Mediterranean regions. Cliff habitats are known to promote speciation and relict endemism through geographical isolation and long-term habitat continuity. Although not particularly rich in species per site (alpha diversity), relicts, as well as neo-endemisms, lead to an extraordinary regional and supra-regional diversity. The large number of floristically well-defined plant communities and alliances reflects these geographical and altitudinal patterns. Apart from the striking biogeographical variation, local-scale differences in species composition occur due to exposure, cliff topography, rock texture, mineral composition and humidity.
Mediterranean base-rich inland cliffs occur in most of the Iberian Peninsula (except the northern part), the Balearic islands, southern France, Corsica, Sardinia, Sicily, the Tyrrhenian coastal region with the islands, the Apennines, the Adriatic and Ionian coastal regions and islands, the southern Balkans (as far as Mediterranean climate is prevailing), the Aegean, Cyprus, further to Mediterranean Turkey (Anatolia) and the Mediterranean parts of Syria, Lebanon, Jordan and Israel, as well as to northern Africa (i.e. Cyrenaica in Lybia, Tunisia, Algeria and Morocco). Non-halophytic cliffs are present from sea-level up to the high mountains, exposed or sheltered, in ravines, gorges, precipices and summit areas. Ultramafic cliffs are included under habitat H3.2g, while halophytic coastal cliffs are included under habitat B3.1-3b.
Indicators of quality:
Mediterranean limestone cliffs are mostly natural habitats with only little or marginal human influence. Mediterranean cliffs support a characteristic chasmophytic flora rich in local and regional endemics. There are several examples of neo-endemics (Quaternary speciation) as well as paleo-endemics (Tertiary relics). The occurrence of rare and phytogeographically significant endemics indicates high quality. Since the chasmophytic flora varies much between areas, the quality of particular sites should be judged by the chasmophytes occurring in the site proportional to those in the wider area.
Cliff habitats are mostly inaccessible and as such to some extent they are naturally protected. Human impacts such as quarrying and rock control structures are tantamount to the destruction of the habitat. The following characteristics may be used as indicators of good quality:
Occurrence of a representative set of rare species, in particular narrow or regional endemics
Presence of different aspects of rock walls, different exposure to insolation, moisture and rock structures such as vertical rock faces, overhangs, cavities, rock shelters and ledges
Contact with natural habitats such as extensive screes, rock shrubs and dry grasslands
Absence of limestone mining and quarrying
Absence of rock control structures
Absence of garbage dumping and nutrient input from above the cliff
Absence of rock climbing facilities

Characteristic species:
Vascular plants: Achillea (ageratifolia subsp. aizoon, cretica, pindicola subsp. integrifolia), Aethionema (lycium, saxatile, schistosum, spicatum), Alchemilla ellenbergiana, Allium (antonii-bolosii, grosii), Allosorus (acrosticus, hispanicus, persicus), Alyssoides cretica, Alyssum (baeticum, cadevallianum), Amelanchier parviflora, Anogramma leptophylla, Antirrhinum (hispanicum subsp. mollissimum, microphyllum, pertegasii, pulverulentum, subbaeticum, valentinum), Anthriscus kotschyi, Arabis (alpina subsp. brevifolia, alpina subsp. caucasica, bryoides), Arenaria (balearica, cretica, deflexa, kotschyana subsp. kotschyana, pamphylica, tmolea, uninervia), Artemisia chamaemelifolia subsp. cantabrica, Asperula (arcadiensis, boissieri, boryana, paui subsp. dianensis, paui subsp. paui, pubescens, serotina, stricta subsp. grandiflora, tournefortii), Asplenium (aegaeum, ceterach, creticum, fissum, fontanum, lepidum subp. lepdium, lepidum subsp. haussknechtii petrarchae, ruta-muraria, sagittatum, seelosii subsp. glabrum, tadei, trichomanes), Asyneuma (compactum, linifolium subsp. linifolium, lycium), Athamanta vayredana, Aubrieta (canescens subsp. canescens, deltoidea, thessala), Aurinia (corymbosa, rupestris subsp. cyclocarpa, saxatilis subsp. orientalis), Bellium bellidioides, Biscutella frutescens, Brassica (balearica, cretica subsp. cretica, cretica subsp. aegaea, cretica subsp. laconica, cretica subsp. nivea), Bubon macedonicum, Bufonia calyculata, Bupleurum (barceloi, kakiskalae), Campanula (affinis, aizoon, celsii, cretica, cymbalaria, isaurica, laciniata, mollis, oreadum, pelviformis, rotundifolia subsp. hispanica, rupestris, rupicola, tubulosa, versicolor), Capparis orientalis, Cardamine plumierii, Carex rorulenta, Carum meoides, Centaurea (argentea, boissieri subsp. mariolensis, cariensis subsp. microlepis, clementei, drabifolia, lancifolia, mariana, ossaea, poculatoris, redempta, resupinata subsp. lagascae, rouyi, saxicola, segariensis), Centranthus ruber subsp. sibthorpii, Cephalaria squamiflora (subsp. balearica, subsp. mediterranea), Chaenorhinum (origanifolium subsp. cadevallii, origanifolium subsp. crassifolium, origanifolium subsp. origanifolium, origanifolium subsp. segoviense, tenellum), Chiliadenus glutinosus, Clinopodium (rouyanum, serpyllifolium subsp. fruticosum), Cosentinia vellea, Crepis (auriculifolia, triasii), Crocus cambessedesii, Cystopteris fragilis, Danthoniastrum compactum, Davallia canariensis, Dianthus (elegans, fruticosus, juniperinus, rupicola, xylorrhizus), Digitalis dubia, Doronicum cacaliifolium, Dorystaechas hastata, Draba (acaulis, lacaitae, lasiocarpa subsp. dolichostyla, scardica), Ebenus cretica, Erodium reichardii, Eryngium ternatum, Erysimum candicum, Euphorbia herniariifolia, Festuca pseudosupina, Ficus carica, Galatella cretica, Galium (canum, crespianum, degenii, erythrorrhizon, fruticosum subsp. ephedroides, fruticosum subsp. fruticosum, graecum), Geranium glaberrimum, Globularia majoricensis, Gnaphalium leucopilinum, Gypsophila montserratii, Helichrysum (crassifolium, heldreichii, melitense, orientale), Helictochloa crassifolia, Hieracium (amplexicaule, arragonense, bourgaei subsp. baeticum, candidum, elisaeanum, humile, laniferum, lawsonii, loscosianum, mixtum, pannosum, sartorianum, scapigerum, texedense), Hippocrepis (balearica, valentina), Hirtellina (fruticosa, lobelii), Hormathophylla reverchonii, Hypericum (aciferum, amblycalyx, jovis, origanifolium, taygeteum), Iberis gibraltarica, Inula (candida, heterolepis, methanaea, oxylepis, parnassica, pseudolimonella, verbascifolia), Jacobaea gnaphalioides, Jankaea heldreichii, Jasione foliosa, Lactuca acanthifolia, Lafuentea rotundifolia, Laserpitium petrophilum, Lepidium villarsii subsp. anticarium, Linaria (anticaria, cavanillesii, verticillata), Linum arboreum, Lomelosia (albocincta, crenata, cretica, hymettia, minoana, variifolia), Macrotomia densiflora, Melica rectiflora, Michauxia tchihatcheffii, Micromeria (filiformis, myrtifolia), Minuartia valentina, Moehringia intricata (subsp. castellana, subsp. intricata, subsp. tejedensis), Myosotis speluncicola, Narcissus calcicola, Naufraga balearica, Nepeta (concolor, phyllochlamys), Odontites linkii, Omphalodes luciliae subsp. cilicica, Onobrychis sphaciotica, Onosma graeca, Origanum dictamnus, Papaver rupifragum subsp. rupifragum, Petrorhagia dianthoides, Petromarula pinnata, Phagnalon (rupestre subsp. graecum, sordidum), Poa cenisia, Polypodium (cambricum subsp. cambricum, interjectum, vulgare), Potentilla (caulescens subsp. caulescens, caulescens subsp. nebrodensis, deorum, kotschyana, pulvinaris, speciosa), Pseudoscabiosa (grosii, saxatilis), Ptilostemon chamaepeuce, Ramonda myconi, Ranunculus (creticus, weyleri), Rhamnus (alpina subsp. fallax, libanotica, pumila, sibthorpiana), Rosularia (libanotica, serrata), Rubia angustifolia, Rupicapnos africana subsp. decipiens, Sanguisorba (ancistroides, cretica, rupicola), Sarcocapnos (baetica subsp. baetica, baetica subsp. integrifolia, crassifolia subsp. speciosa, enneaphylla subsp. saetabensis, pulcherrima), Satureja parnassica, Saxifraga (biternata, bourgaeana, camposii, corsica subsp. corsica, corsica subsp. cossoniana, cuneata, exarata, federici-augusti subsp. grisebachii, fragilis subsp. fragilis, fragilis subsp. paniculata, glabella, granatensis, kotschyi, latepetiolata, longifolia subsp. longifolia, losae, luteoviridis, marginata, moncayensis, paniculata, porophylla, reuteriana, rigoi, scardica, sempervivum, sibthorpii, spruneri, taygetea), Scorzonera cretica, Scrophularia (depauperata, heterophylla, kotschyana, libanotica), Scutellaria sieberi, Securigera globosa, Sedum (dasyphyllum subsp. dasyphyllum, dasyphyllum subsp. glanduliferum, dasyphyllum subsp. granatense, magellense), Selaginella denticulata, Sempervivum marmoreum, Senecio castagneanus, Sesleria (doerfleri, insularis), Sibthorpia africana, Sideritis (glauca, perfoliata, stachydioides), Silene (andryalifolia, auriculata, boryi, congesta, gazulensis, gigantea, hifacensis, leptoclada, mollissima, odontopetala, parnassica, pusilla, saxifraga, tomentosa), Solenopsis balearica, Stachys (candida, chrysantha, parolinii, spreitzenhoferi, swainsonii), Staehelina petiolata, Symphytum creticum, Tanacetum (argenteum subsp. canum, argenteum subsp. flabellifolium, armenum), Teucrium (aroanium, buxifolium subsp. buxifolium, cuneifolium, fragile, francisci-werneri, freynii, halacsyanum, hifacense, intricatum, rivasii, rivas-martinezii, rotundifolium subsp. rotundifolium, thymifolium), Thymus richardii (subsp. ebusitanus, subsp. richardii), Trisetum velutinum, Umbilicus (horizontalis, luteus, rupestris), Valeriana (apula, asarifolia, longiflora, sisymbriifolia, speluncaria, tripteris), Verbascum (arcturus, pestalozzae), Veronica (bellidioides subsp. lilacina, kotschyana), Viola (chelmea, herzogii, parnonia, perinensis, poetica).
Bryophytes: Anoectangium aestivum, Anomodon viticulosus, Didymodon vinealis, Brachythecium glareosum, Brachythecium laetum, Bryum elegans, Ctenidium molluscum, Distichium capillaceum, Ditrichum flexicaule, Distichium inclinatum, Encalypta streptocarpa, Encalypta vulgaris, Frullania tamarisci, Gymnostomum calcareum, Grimmia anodon, Grimmia capillata, Grimmia crinita, Grimmia orbicularis, Grimmia teretinervis, Grimmia tergestina, Gymnostomum aeruginosum, Gymnostomum viridulum, Gyroweisia tenuis, Homalia trichomanoides, Homalothecium lutescens, Homalothecium philippeanum, Homalothecium sericeum, Isothecium myosuroides, Leiocolea collaris, Mnium marginatum, Mnium stellare, Myurella tenerrima, Neckera complanata, Neckera crispa, Orthotrichum anomalum, Orthotrichum cupulatum, Plagiochila exigua, Plagiochila spinulosa, Porella platyphylla, Pseudoleskea incurvata, Pseudoleskeella catenulata, Pterogonium gracile, Reboulia hemisphaerica, Schistidium apocarpum, Schistidium brunnescens, Schistidium crassipilum, Seligeria calcarea, Targionia hypophylla, Timmia bavarica, Tortella tortuosa, Tortula calcicolens, Tortula crinita, Tortula muralis, Tortula norvegica, Tortula ruralis, Trichostomum crispulum.

Classification:
EUNIS:
H3.2 Basic and ultra-basic inland cliffs
EuroVeg Checklist:
Adiantion Br.-Bl. ex HorvatiÄ‡ 1934
Amphoricarpion neumayeri LakušiÄ‡ 1968
Arenarion balearicae O. de Bolòs et Molinier 1969
Arenarion bertolonii Gamisans ex Theurillat in Mucina et al. 2014
Arenarion creticae Dimopoulos, Sýkora, Mucina et Georgiadis ex Bergmeier 2002
Asperulion garganicae Bianco et al. 1989
Asplenio celtiberici-Saxifragion cuneatae Rivas-Mart. in Loidi et Fernández Prieto 1986
Asplenion glandulosi Br.-Bl. in Meier et Br.-Bl. 1934
Asterion cretici Zaffran ex Bergmeier et al. 2011
Aubrietion olympicae Quézel et PamukçuoÄŸlu 1970
Brassicion insularis Gamisans 1991
Brassico balearicae-Helichrysion rupestris O. de Bolòs et Molinier 1958
Campanulion cymbalariae Hein et al. 1998
Campanulion isauricae Hein et al. 1998
Campanulion velutinae Martínez-Parras et Peinado Lorca 1990
Campanulion versicoloris Quézel 1964
Capparo-Amaracion tournefortii Horvat in Horvat, GlavaÄ et Ellenberg ex Bergmeier et al. 2011
Caro multiflori-Aurinion megalocarpae Terzi et D'Amico 2008
Centaureo dalmaticae-Campanulion HorvatiÄ‡ 1934
Centaureo filiformis-Micromerion cordatae Arrigoni et Di Tommaso 1991
Centaureo-Portenschlagiellion TrinajstiÄ‡ 1980
Cosentinio bivalentis-Lafuenteion rotundifoliae Asensi et al. 1990
Dianthion rupicolae S. Brullo et Marcenó 1979
Drabion acaulis Hein et al. 1998
Edraianthion LakušiÄ‡ 1968
Galion degenii Quézel 1967
Inulion heterolepidis Horvat in Horvat, GlavaÄ et Ellenberg ex Bergmeier et al. 2011
Jasionion foliosae O. de Bolòs 1957
Micromerion croaticae Horvat et al. 1974
Onosmion mutabilis Quézel 1973
Petrocoptidion glaucifoliae (P. Fernández et al. 1983) Rivas-Mart., Cantó et Izco in Rivas-Mart. et al. 2002
Petromarulo-Centaurion argenteae Horvat in Horvat, GlavaÄ et Ellenberg ex Bergmeier et al. 2011
Pinguiculion longifoliae Fernandez Casas 1970
Polypodion serrati Br.-Bl. in Br.-Bl. et al. 1952
Sarcocapnion enneaphyllae Fernandez Casas 1972
Sarcocapnion pulcherrimae Fernandez Casas 1972 corr. Rivas-Mart. et al. 2002
Saxifragion australis Biondi et Ballelli ex S. Brullo 1984
Saxifragion camposii Cuatrecasas ex Quézel 1953
Saxifragion scardicae Dimopoulos et al. 1997
Silenion auriculatae Quézel 1964
Silenion odontopetalae Quézel 1973
Teucrion buxifolii Rivas Goday 1956
Valeriano longifoliae-Petrocoptidion Fernandez Casas 1972
Centaureion pentadactyli Brullo, Scelsi et Spampinato 2001
Athamantion dellae-cellae Brullo et Furnari 1996
Terucrion cyrenaici Brullo et Furnari 1996
Annex 1:
8210 Calcareous rocky slopes with chasmophytic vegetation
Emerald:
H3.2 Basic and ultra-basic inland cliff
MAES-2:
Sparsely or unvegetated land
IUCN:
6. Rocky areas

Justification Outstanding Example of Biogeographical Region:
The habitat represents an outstanding example of the Mediterranean biogeographic region as a result of the occurrence of a pool of species, mostly endemic, characterized by a high ecological specialization and a remarkable phytogeographical, genetic and evolutionary value.

Map Description:
The map is rather complete, except for some possible occurrences on the eastern side of the Adriatic sea. Data sources: Art17.

Comment EU28+:
These figures are calculated without considering data from Cyprus and Albania, as it was not available.

Trends in Quantity:
Based on the provided data, the reduction of this habitat type over the last 50 years is 0.4% for both the EU 28 and for the EU 28+. Thus, it can be considered stable. Although no figure or estimation can be provided for future trends, its future extent trends can be realistically considered as stable.

Trends in Quality:
Past, historical and future trends cannot be estimated due to the lacking of data. In addition, when provided, data are incomplete and thus, not adequate to calculate reliable trends in quality. The extent and severity of degradation are both unknown.

% of Distribution of the Habitat Type within the EU 28:
More than 90% of the current distribution of this habitat type lies within the EU 28.

Justification of Small Range/Regression:
There has been no relevant regression over the last 50 years.

Justification of Restricted Area:
This habitat cannot occur everywhere since its establishment requires very specific climatic and geo-morphological features. Therefore, the total area occupied is naturally very limited.

Pressures and Threats:
This habitat type is not very affected by human activities, especially on mountain stands and rather inaccessible sites. Despite this fact, some disturbances may be caused by sport and leisure activities (e.g. rock-climbing), mining and quarrying (at lower elevations), invasive and/or alien plants (at low altitudes), and cliff securing.

Conservation and Management:
The best management practice for this highly natural habitat is to leave it simply untouched, thus avoiding any human interference with its natural processes. Luckily, cliffs are mostly present in protected areas.
Information about the biological value of this habitat to the potential users, such as climbers, should be extensively provided. In addition, public awareness about the biological relevance of such apparently inhospitable environments should be increased.

Capacity to Recover its Typical Character and Functionality?:
Unless completely destroyed, cliff recovery is possible provided that it is potentially connected with similar environments and that natural geo-morphological processes are not hampered. As many specialised plants of this habitat type are poor dispersers, the species composition is expected to remain impoverished even after initial habitat recovery.

Summary:
This habitat is composed of cliffs of limestone, calcareous conglomerates and other base-rich rocks in the lowlands to high mountains through the Mediterranean (excepting in salt-sprayed coastal situations). They are characterised by a diverse flora of calcicole vascular perennial plants, often of rosulate, prostrate, succulent and cushion form, tussock grasses, small ferns, dwarf shrubs, shrubs and sometimes woody climbers and small trees, rooted in fissures and crevices. There are also bryophytes, lichens and epi- and endolithic micro-organisms. Towards the foothills and lowlands, the habitat is more prone to be affected by human disturbances, especially its species composition. High mountain cliffs are usually well preserved, with a high degree of naturalness. Threats are mainly linked to securing cliffs alongside roads and rail, sport and leisure activities (e.g. rock-climbing) and, especially at lowere elevations, mining, quarrying and invasive/alien plants. Public awareness raising and scientifically-based management of this habitat type is needed.

References:
Brullo, S., Marcenò, C. and Siracusa, G. 1998. La classe Asplenietea trichomanis in Sicilia. Colloques Phytosociologique 28: 467-538.
Quézel, P. 1964. Végétation des hautes montagnes de la Grèce méridionale. Vegetatio 12: 289–386.

Criterion A Text:
A decline of 0.4% has been calculated over the past 50 years. There is no information on future and historic declines. Therefore, the habitat type is assessed as Least Concern under Criterion A.

Criterion C/D Text:
There is no information on past, historical and future reductions in quality, and thus the habitat is assessed as Data Deficient under Criterion C/D.

Synthesis:
The habitat type is assessed as Least Concern status (LC) in view of its stable trend, since a reduction of only 0.4% has occurred over the last 50 years. Reductions in quality cannot be estimated due to lack of information. Future trends for this habitat are rather unpredictable, but most of the Mediterranean cliffs fall within natural reserves or protected areas and thus are presumed to be stable.

Sub-habitats in Need of Examination:
No subhabitats have been distinguished, but it is clear for the high number of alliances that the habitat contains large diversity, and several regional subtypes may be distinguished.

Contributors:
Type description: E. Bergmeier & G. Giusso del Galdo
Territorial data: E. Agrillo, O. Argagnon, F. Attorre, S. Bagella, J. Capelo, A.ÄŒarni, L. Casella, D. Espírito-Santo, D. Gigante, G. Giusso del Galdo, J. Loidi, C. Marcenò, D. Milanovic, S. Sciandrello, Z. Škvorc, D. Viciani
Working Group Sparsely Vegetated Habitats: F. Essl, G. Giusso Del Galdo, A. Mikolajczak, D. Paternoster, M. ValachoviÄ, M. Valderrabano


Habitat Description:
Xerophytic nano- to microphanerophytic communities, sclerophyllous, succulent (or having other kinds of morphological adaptations to drought) of the lower altitudes in Madeira island. These include: (1) communities dominated by paleomediterranean shrubs or small trees: Olea, Maytenus, Chamaemeles: with hard leathery leaves (Mayteno-Oleion maderensis) that stand for mature zonal vegetation of permanent character in thin cambisols of rocky steep cliffs in the infra to thermomediterranean (sometimes infra-thermotemperate in the north face) semi-arid to dry belts. In their upper altitude limit some of these communities (Myrtus communis with Hypericum canariense) may be the natural edge or first seral stage of the Apollonias barbujana thermomediterranean sub-humid forests (included in G2.3 type, Visneo-Apollonion); (2) Thick succulent stemmed Euphorbia piscatoria summer-deciduous communities that are seral stages of the former (i.e. i)), permanent communities or pioneer in rocky leptosols, for instance in low altitude abandoned fields; (3) inframediterranean/temperate sub-humid half-sclerophyllous tall shrub communities of the northern face, transitional from xerophytic to mesophytic heathlands (Syderoxylon mirmulans community: Visneo-Apollonion barbujanae); (4) chamaephytic communities of neomediterranean shrubs, having rolled, hairy, waxy or resinous leaves, or exhibiting leaflessness the most part of the year, that are seral stages of the zonal sclerophyllous types, pioneer or sometimes permanent in semiarid steep rocky cliffs (Soncho-Artemision argenteae); (5) xerophytic succulent low-scrub semi-halonitrophyllous under some influence of salt winds and nitrates from bird dropping deposition of Calendula maderensis (Argyranthemo suculenti-Calendulion maderensis).
The two later variants (iv) and v)) could be together separated as a subtype within the F8.2 type, but since they are found usually in mosaic with the other variants without regional or landscape separation, this is superfluous for habitat typology purposes. The main contacts of the F8.2 type are with Grenovio-Aeonietea succulent rock wall vegetation (Sinapidendro-Aeonion glutinosi, H3.3 Macaronesian inland cliffs). Where the semi-halonitrophyllous scrubs are not found in mosaic with other communities of H8.2, they can be considered as type H6.8a Mediterranean halo-nitrophilous scrubs.
Indicators of good quality:
In general, dominant plants and the bioindicator set should be identified at its maximum mumber as a measure of ecological integrity (see characteristic species, flora, vascular plants). As to the sclerophyllous or half-sclerophyllous variants (i and ii) that are successionaly replaced by the ii) or iv) variants by disturbance, the more elements of Euphorbia piscatoria community (E. piscatoria, Echium nervosum or Globularia salicina) or any of the iv) variant (Carlina salicifolia, Artemisia argentea, Erysimum maderense, Genista tenera, Helichrysum monizii, Micromeria varia subsp. thymoides and Phagnalon lowei), the more the sclerophyllous i) variant is formally close to collapse. Nevertheless, since this happens from natural or expected human-induced causes and the seral stages are themselves floristically valuable, some care should be taken in evaluating the whole of the mosaic of variants within the F8.2 type for conservation purposes. The same reasoning applies to the v) variant (indicators: Argyranthemum pinnatifidum subsp. suculentum and Calendula maderensis). Reliable indicators of degradation are the increase in dominance of tall-grass stages: Hyparrhenia sinaica (=H. hirta auct mad.), Cenchrus ciliaris, Dactylis glomerata subsp. hylodes or any kind of disturbance-prone or nitrophyllous vegetation.
Note on delimitation of habitat type
We restrict the habitat concept to the xerophytic hard-leaved/succulent in low-altitude (infra-thermomediterranean) semi-arid to dry nano-microphanerophytic shrub communities (Rhamno-Oleetea cerasiformis) and also including xerophytic low-scrub in high sea cliffs under the moderate influence of salt winds and nitrates from sea bird droppings (semi-halonitrophyllous communities: Pegano-Salsoletea). Due to its transitional character between xerophytic high scrub (Mayteno-Oleion) and driest /hottest laurel forest (Visneo-Apollonion), the Sideroxylon mirmulans tall-scrub is also included in the type. Chamaephytic communities of salt-rich soil in sea-cliffs under strong influence of salt spray close to wave breaks are not included (Helichrysio obconico-devium) and belong to habitat type B3.1-3c – Macaronesian rocky sea cliffs and shores. Also, chamaephytic vegetation dominated by succulent crassulaceae (Aeonium sp. pl.) is excluded and considered in H3.3.- Macaronesian inland cliffs.
Characteristic species:
Flora
Vascular plants: Olea maderensis (Lowe) Rivas Mart. & Del Arco (dom.), Rubia fruticosa subsp. fruticosa, Asparagus scoparius, Bupleurum salicifolium subsp. salicifolium, Ephedra fragilis var. dissoluta, Erysimum bicolor, Globularia salicina (dom.), Hypericum canariense var. floribundum (dom.), Jasminum odoratissimum, Myrtus communis, Tamus edulis, Teucrium heterophyllum, Asparagus umbellatus subsp. lowei, Chamaemeles coriacea*, Convolvulus massoni, Crambe fruticosa, Echium nervosum (dom.), Echium portsanctensis, Euphorbia piscatoria (dom.), Sideroxylon mirmulans (dom.), Helichrysum melaleucum, Jasminum azoricum, Maytenus umbellata (dom)., Plantago maderensis, Prasium medium, Scilla madeirensis, Sideritis candicans var. multiflora, Carlina salicifolia, Artemisia argentea, Cheirolophus massonianus, Erysimum arbuscula, Erysimum maderense, Genista tenera, Helichrysum monizii, Lotus argyrodes, Lotus macranthus, Micromeria varia subsp. thymoides var. thymoides, Phagnalon lowei, Atriplex glauca subsp. ifnensis, Atriplex halimus, Chenoleoides tomentosa, Launea arborescens , Lycium intricatum, Lavandula pinnata, Schizogyne sericea, Argyranthemum pinnatifidum subsp. suculentum, Calendula maderensis.
* this genus is endemic to Madeira.

Classification:
EUNIS:
F8.2 Xerophytic scrub of Madeira
EuroVegChecklist:
Mayteno umbellatae-Oleion maderensis (whole)
Soncho ustulati-Artemision argenteae (whole)
Argyranthemo suculenti-Calendulion maderensis (whole)
Visneo mocanerae-Apollonion barbujanae (a small part: Helychryso melaleuci-Sideroxyletum mirmulans)
Annex 1:
-
Emerald:
-
MAES-2:
Heathland and shrub
IUCN:
3.5. Subtropical/Tropical Dry Shrubland

Justification Outstanding Example of Biogeographical Region:
The habitat type is restricted to rock walls  in the low-altitude southern face of Madeira Island (with few empoverished location in the northern face). It is dominated by endemic shrubs: Olea maderensis, Maytenus umbellata, Echium nervosum, Euphorbia piscatoria. And even includes an endemic genus: Chamaemeles Lindl.

Map Description:
The map provides the complete distribution of the habitat. Data sources: LIT.

Trends in Quantity:
Although one of the variants of the habitat, probabily has somewhat recovered in the last two decades due to abandonment of traditional agricultures (the Euphorbia piscatora-dominated variant ii) ), the genearl trend is estimated to be of a severe reduction in the  50 year time span. The assesor's estimate is of - 85% area reduction, in this period, due to a great urban expansion since 1974 taking place in the lower altitudes of the southern face of the island (which is the optimum area of the habitat). Historical reduction was not reported, but assessors by comparing the potential area (Natural Potential Vegetation Map) and the actual area and agricultural historical records estimate that reduction might have been greater than 50%. Future trends is that the rate of area reduction is much lower due to conservation policies, but as conflicts with urban expansion still are expected, the absolute area of habitat might descrease all the same.

Trends in Quality:
There is no territorial information to evaluate any of the parameters to estimate quality reduction. Assessors estimate a decrease as average current trend.

% of Distribution of the Habitat Type within the EU 28:
The whole of the habitat area is within the EU28

Justification of Small Range/Regression:
The habitat has a small (EOO =2.380 Km2) range (AOO = 8 (eight) 10 x 10 gridsquqres) and has suffered a great reduction in the last 50 years (85%).

Justification of Restricted Area:
The habitat has a small (EOO =2.380 Km2) range (AOO = 8 (eight) 10 x 10 gridsquqres).

Pressures and Threats:
The main threat is urban expansion, due to buildings and infrastructure associated to transport. Further, stabilization of rock walls and steep slopes by engineering procedures often leads to degradation or collapse of sites with the habitat. Finally, the invasion of alien species is also a threat, like reeds (Arundo donax) and exotic cactusses (Opuntia tuna).

Conservation and Management:
Restoration of Madeirean xerophytic scrub should follow the following principles:
1. Establishment of protected areas (micro-reserves) with strict protection of habitat sites and component species as many small locations are within urban or semi-urban context.
2. Removal of pressures or any kind of human-induced disturbance.
3. Removal of alien invaders
4. Allow urban development to take such micro-reserves in account with a buffer around them.

Capacity to Recover its Typical Character and Functionality?:
Although some of the characteristic species may establish relatively quickly, it is assessed that recovery to a species-rich, natural vegetation takes relatively long.

Summary:
This endemic scrub of succulent shrubs and small trees is confined to rocky lowland cliffs on Madeira, including both primary vegetation, degraded serial stages and transitions to halophytic scrub, heathland and forest. It is strongly threatrened by urban development with most locations being very small and embedded in an urban or semi-rural landscape, and also by invasion of non-native grasses and cacti. The creation of miniature reserves and mitigation of impacts are essential.

References:
CAPELO, J., J. C. COSTA, M. LOUSÃ, S. FONTINHA, R. JARDIM, M. SEQUEIRA & S. RIVAS-MARTÍNEZ (2000).
Vegetação da Madeira (Portugal): aproximação à tipologia fitossociológica. Silva Lusitana 7(2) : 257 – 279.
CAPELO, J., M. SEQUEIRA, R., JARDIM, S. MESQUITA & J. C. COSTA (2005) The vegetation of Madeira Island
(Portugal). A brief overview and excursion guide. Quercetea 7: 105 -122
COSTA, J.C., C.NETO, C. AGUIAR, J. CAPELO, M.D. ESPÍRITO-SANTO, J. HONRADO, C. PINTO-GOMES, T.
MONTEIRO-HENRIQUES, M. SEQUEIRA & M. LOUSÃ (2012) Vascular Plant Communities in Portugal
(continental, Azores & Madeira) Global Geobotany 2: 1 -180.
COSTA, J.C., J. CAPELO, R. JARDIM, M. SEQUEIRA, D. ESPÍRITO-SANTO, M. LOUSÃ, S. FONTINHA, C. AGUIAR &
S. RIVAS-MARTÍNEZ in CAPELO, J. (ed.) (2004) Catálogo sintaxonómico e florístico das comunidades
vegetais da Madeira e Porto Santo. Quercetea 6: 61-186.

Criterion A Text:
Over a 50-year time span a reduction in its area is estimated of -85% due to recent urban development. Historical reduction is estimated to be large as well, due to urban and agricultural land use and, surely, larger than 50% of the original area. Future trends are expected to be of lower reduction rates, as protection measures were issued, although conflicts with urban development objectives are still to be expected. A slight further decrease of the already critical area is therefore not unrealistic. The figures lead to the category Endangered (EN) for A1 and Vulnerable (VU) for A3.

Criterion B Text:
The habitat range is small (EOO=4550 Km2) and the same goes for the distribution (AOO = 14 grid cells). The number of 10 x 10 km locations is likely not to have declined, but a large reduction in area (inside the grid cells) has occurred. Some reduction due to urbanistic pressure is still to be expected in spite of protective measures, so criteria B1a and b apply. These figures lead to the category Endangered (EN) for B1 and B2.

Criterion C/D Text:
No territorial data were available, but based on expert knowledge it is estimated that a reduction in quality occurred over the last 50 years in 30% of the area with moderate severity (50%), mainly caused by invasion of non-native plant species. This assessments just leads to the category Near Threatened (NT).

Synthesis:
The very large reduction in area (-85%) over a 50 year timespan due to urban expansion leads to the Red List category Endangered (EN) under criterion A1. The same category is assessed from the very restricted geographic distribution (both in extent and area of distribution) in combination with continuing negative trends and threats (criteria B1 and B2).

Sub-habitats in Need of Examination:
Several varieties with a high risk of extinction may be distinguished. The Euphorbia piscatoria subtype is likely to be the less threatened subtype, as it develops from agricultural abandonment. All other subtypes however have a small area and

Contributors:
Habitat definition: J. Capelo
Territorial data: J. Capelo & Dalila Espírito-Santo (with collaboration of Miguel Sequeira and Roberto Jardim)
Working Group Heathland & Scrub: M. Aronsson, F. Bioret, C. Bita-Nicolae, J. Capelo, A. ÄŒarni, P. Dimopoulos, J. Janssen, J. Loidi


Habitat Type Name:
A5.61: Polychaete worm reefs in the Mediterranean infralittoral zone

Habitat Description:
Worm reefs are large bioconstructions built by polychaetes the most important of which in the Mediterranean are the sabellarids Sabellaria alveolata and S. spinulosa and the serpulids Hydroides dianthus and Ficopomatus enigmaticus. The development of such reefs is assured by the gregarious settlement of polychaete larvae, which occurs mainly on pre-existing reefs or their dead remains. 
Sabellaria bioconstructions can be relatively unstable and undergo a natural cycle of development and decay, they can form relatively quickly and may take the form of sheets, hummocks and reefs as well as evolving from globular formations into reef platforms. Reefs may persist in an area for many years although individual clumps may regularly form and disintegrate.  Sabellaria alveolata reefs in the Mediterranean are located between 1 to 7 m of depth where can reach 60 cm thick when they are well developed. In most sites, however, they tend to be very scattered and not particularly extensive
Most serpulids are considered to be 'secondary frame builders'. Ficopomatus enigmaticus, typically growing in coastal lagoons and brackish water lakes, can form large reefs. They can occur as a fringing reef along the rocky shoreline, forming a continuous layer that can reach up to 3 m thick, at a depth of about 1 m, or can develop as dense patch reefs growing from the bottom, with hemispherical forms called micro atolls (over 2 m height and 4 m in diameter) and with a distribution related to the depth (from 0.5 to 1.5 m).
This habitat provides a diversity of microhabitats increasing available substrate for numerous species; sheltering both hard and soft-bottom rare species which are potential colonizers of adjacent habitats; providing refuge for invertebrates including snails and crabs that may have an impact on native species communities and are attractive for some fish such as  Sygnathus abasteri, Aphanius fasciatus and Knipowitschia panizzae
Indicators of quality                                                                                                                              
The status and dynamics of the reefs must be defined integrating the physical characteristics, taking into account the degree of fragmentation of reef features (mainly produced by species which are known to degrade, smother and break up areas of Sabellaria, e.g. the mussel Mytilus galloprovinciallis), and the prevalence of different structural characteristics within the reef formations. The health of the reefs can  be determined with reference to the percentage of newly settled worms, those with crisp apertures, those with worn apertures and dead worms. 
Characteristic species:
The associated fauna in S. alveolata reefs is rich and diversified. The most abundant species are Apseudes latreillii, Quadrimaera inaequipes, Leptochelia savignyi, and Monocorophium sextonae, among crustacean and Striarca lactea among mollusc. Abundant species of polychaete are Nereis falsa and Eulalia ornate.
Ficopomatus enigmaticus is the primary builder in the serpulid reefs. Its tubes form the bases of the biocontruction, but other organisms such as the barnacles Balanus eburneus and B. amphitrite, and the molluscs Mytilaster lienatus and M. marioni can contribute to the reef formation and can be treated as secondary builders. Other organisms such as the bryozoan Conopeum seurati, can stabilize the formation with its encrusting colonies which cementate the tubes. Other colonial organisms such as the hydroid Cordylophora cassia, the bryozoan Bowerbankia gracilis, and the tunicate Botryllus schlosseri can simply colonize this secondary substrate. The reef can host a lot of vagile invertebrates such as isopods (Lekanesphaera hookeri, L. monody, Sphaeroma serratum, C. ascherusicum) and gammarids (Gammarus aequicauda, G. insensibilis) and other polychaetes such as Hediste diversicolor, Neanthes succinea, and several polydorids

Classification:
EUNIS (v1405):
Level 4. A sub-habitat of ‘Mediterranean infralittoral biogenic habitat’ (A5.6).
 
Annex 1:
1170 Reefs
 
MAES: 
Marine - Marine inlets and transitional waters
Marine - Coastal
 
MSFD:
Shallow sublittoral rock and biogenic reef
Shallow sublittoral sand
 
EUSeaMap:
Shallow photic rock or biogenic reef
Shallow aphotic rock or biogentic reef
Shallow coarse or mixed sediments
 
IUCN:
9.2 Subtidal rocky and rocky reefs
9.4 Subtidal sandy
 
Barcelona Convention (RAC/SPA):
III. 1. 1. 2. Facies with Ficopomatus enigmaticus

Map Description:
This map has been generated using data based on Bianchi et al.,1995; Giangrande, A. et al., 2012. and IUCN EOO and AOO have been calculated on the available data presented in this map however these should be treated with caution as expert opinion is that this may not indicate the full distribution of the habitat.

Comment EU28:
EOO and AOO have been calculated on the available data but this is known to be incomplete.

Comment EU28+:
EOO and AOO have been calculated on the available data but this is known to be incomplete.

Trends in Quantity:
The knowledge on Mediterranean reefs is too fragmentary to evaluate their distribution and quantity especially concerning Sabellaria. As far as Ficopomatus a surface area of  6 km2  was computed  along Ligurian coast.

Trends in Quality:
The status and dynamics of the reefs can be defined integrating the physical characteristic, taking into account the degree of fragmentation of reef features, cover by species which are known to degrade, smother and break up areas of Sabellaria reef (mainly by the mussel Mytilus galloprovincialis) and the prevalence of different structural characteristics within the reef formations. The health of the reefs is determined with reference to the percentage of newly settled worms, those with crisp apertures, those with worn apertures and dead worms.  The degradation and recovery of the two builder Sabellaria species that occurs as a response to external environmental pressure, can be different according to the two different life-cycles. Sabellaria alveolata can live up to 9 years, whilst S. spinulosa is a fast growing annual species.
There is very limited information regarding the trends on the quality of this habitats. Present knowledge on Mediterranean reefs is too fragmentary to define their dynamics, previous knowledge allows little or no temporal comparison.

% of Distribution of the Habitat Type within the EU 28:
Unknown. Only information regarding the distribution of this habitat in EU is available. Large biogenic formations of S. spinulosa had been found along the Adriatic coast (from Ancona to Gargano, Italy).

Pressures and Threats:
Sabellaria reefs are highly dynamic habitats subject to numerous natural perturbations, they are also increasingly threatened by direct and indirect anthropogenic disturbances including colonization by mussels and oysters from local aquaculture, development of ephemeral green algae in response to eutrophication or physical degradation of the reef through trampling and shellfish farming. These disturbances may cause significant damages to the reef structures with also a reduction in density of new recruits. Sabellaria reefs are highly vulnerable and sensitive; both fishing and associated trampling can seriously damage this fragile habitat. Moreover alien introduced species have potential impact on them. Sabellaria reefs can take many years to recover, and some may never recover.   
Ocean warming and acidification can decraese net calcification in Ficopomatus reef, decreasing growth and reproduction as well as reduction of abundance and diversity.

Conservation and Management:
Knowledge of this habitat is too fragmentary to determine their current health status and to define their dynamics, in order to evaluate the most important threats and impacts, to highlight the conservation needs and suggest management measures and protection actions. Understanding those parameters that influence the reef dynamics is necessary in order to develop efficient and effective management practices and policy focusing on the conservation status of large biogenic structures.

Capacity to Recover its Typical Character and Functionality?:
Serpulid reefs built by Ficopomatus are extremely dynamic in both space and time, and are characterized by very short-cycles, because they form in brackish water dynamic environment. The reefs break-down under their own weight and reform continuously.  Therefore Ficopomatus  is able to respond to the environmental changes and recover from damage in relatively short time. However, important variation in water flow regime and quality (especially salinity), and high human pressure  can led to the disappearance of these reefs and reduce their recover capacity.
Sabellaria reefs are extremely dynamic too, they may persist in an area long time although individual clumps may regularly form and disintegrate. Usually,  reefs show a cycle of development undergoing 4 different easily determined morphologies (reef compactness, tube orientation, percentage of tubes with 'sand crown', and presence/absence of epibionts on the reef surface) and defined as 'phases'. Each phase is the result of a constantly disturbed and precarious balance between physical factors (hydrodynamic forces, temperature, and local environmental conditions, such as seabed topography and water clarity), and biological factors (reproduction and recruitment mechanism of the pelagic larvae). Sabellaria alveolata can live up to 9 years, whilst S. spinulosa is a fast growing annual species so that degradation and recovery of the reefs that occurs as a response to external environmental pressure, can be different, even if in both species recruitment rates are high and recovery could be quite rapid, the speed of changes is different according to their different life cycle. As a consequence S. alveolata reefs seem to be more persistent and more abundant than S. spinulosa which, in most parts of its geographic range, is solitary or form small groups.  
The limited understanding of the factors affecting recruitment success and of the source of larval supply preclude further predictions on the potential for recovery and the rate at which it might occur.  Biogenic reefs can take many years to recover, and some may never recover. For example, Sabellaria spinulosa reefs have failed to recover in the Wadden Sea following their dramatic decline over recent decades. According to the life-cycle knowledge it can be hypothesised that the recover of S. alveolata may occur within at least 10 years if condition are maintained optimal, but that can last more time naturally.

Summary:
In the Mediterranean area, worm reefs are built by the sabellarids Sabellaria alveolata and S. spinulosa and the serpulids Hydroides dianthus and Ficopomatus enigmaticus. Their development  is assured by the gregarious settlement of polychaete larvae, which occurs mainly on pre-existing reefs or their dead remains. In confined brackish-water habitats, bioconstructions made by the dense accumulation of the serpulid calcareous tube builders, can occur as fringing reefs along the shoreline, or can develop as dense patch reefs growing from the bottom. The filtration activity of these worms can condition the trophic state of  entire lagoon ecosystems. 
Worm reefs are highly vulnerable and sensitive to direct and indirect anthropogenic disturbance. Both fishing and associated trampling and intensive mussel cultivations can seriously damage this fragile habitat. Moreover alien introduced species and acidification can have potential impact on them. Their reefs, which often act as nurseries for many coastal species, can take many years to recover, and some may never recover. Understanding those parameters that influence the reef dynamics is necessary in order to develop efficient and effective management practices and policy focusing on the conservation status of large biogenic structures.

References:
Bianchi e Morri.2001. The Battle is not to the Strong: Serpulid Reefs in the  Lagoon of Orbetello (Tuscany, Italy). Estuarine, Coastal and Shelf Science 53: 215-220.
Camus, P., Compere, Ch., Blanchet, A., Dimeet, J., Hamon, D., Lacotte, N., Peleau, M. et Lasalle, E., 2000. Ficopomatus enigmaticus: écologie, répartition en France et Bretagne, nuisances et moyens de lutte sur le site atelier du port de Vannes. Rapport de contrat Ifremer – Ville de Vannes, 50 p. (Thau Francia)
Cukrov, M., DespalatoviÄ‡, M., Å½uljeviÄ‡, A., Cukrov, N., 2010. First record of the introduced fouling tubeworm Ficopomatus enigmaticus (Fauvel, 1923) in the Eastern Adriatic Sea, Croatia. p. 483-483. In: 39th CIESM Congress, Venice, 10-14 May 2010. CIESM, Monaco.
Delbono, I., Bianchi, C. N., Morri, C. 2003. Le biocostruzioni di Sabellaria alveolata come indicatori ambientali: area costiera fra Chiavari e Sestri Levante. In: Studi per la creazione di strumenti di gestione costiera: Golfo del Tigullio (O. Ferretti, ed.). ENEA, Centro Ricerche Ambiente Marino, La Spezia: 130-140.
Dubois, S., Retiere, C. & Olivier, F. 2002. Biodiversity associated with Sabellaria alveolata (Polychaeta: Sabellariidae) reefs: effects of human disturbances. Journal Marine Biological Association U.K., 82: 817-826.
Ergen, Z. 1976. Investigations on the taxonomy and ecology of Polychaeta from Izmir Bay and its adjacent area. Scientific Reports of the faculty of Science Ege Universityâ€‹, 209: 1-66.
European Environment Agency. 2014. EUNIS habitat type hierarchical view [online]. Available at: http://eunis.eea.europa.eu/habitats-code-browser.jsp [accessed August 2014].
Giangrande A, Cosentino A, Lo Presti C, Licciano M., 2012. Sabellidae (Annelida) from the Faro coastal lake (Messina, Ionian Sea), with the first record of the invasive species Branchiomma bairdi along the Italian coast. Mediterranean Marine Science 13: 283–293, http://dx.doi.org/10.12681/mms.310
Gruet, Y. 1986. Spatio-temporal changes of sabellarian reef built by the sedentary polychaete Sabellaria alveolata (Linné) - PSZN I: Marine Ecology, 7(4): 303-319.
Iaciofano, D., Musco, l., Vega, F., Lo Brutto, S. 2015. Crostacei anfipodi associati a reef di Sabellaria alveolata (L.) (Annelida) dello Stretto di Sicilia (Mar Mediterraneo): Biologia Marina Mediterranea 22(1):95-96.
La Porta Barbara and Nicoletti Luisa 2009. Sabellaria alveolata (Linnaeus) reefs in the central Tyrrhenian Sea (Italy) and associated polychaete fauna. Zoosymposia 2: 527–536.
Lezzi ,M. F., Cardone , B. Mikac, A. Giangrande 2015. Variation and ontogenetic changes of opercular paleae in a population of Sabellaria spinulosa (Polychaeta: Sabellaridae) from the South Adriatic Sea,with remarks on larval development. Scientia Marina 79 (1): 1-14.
Martinez-Taberner, A.; Forteza, V.; Fornos, J. J., 1993: Colonization, structure and growth of Ficopomatus enigmaticus cf. Ten Hove & Weerdenburg (Polychaeta, Serpulidae) in the Albufera of Menorca, Balearic Islands. Internationale Vereinigung fuer Theoretische und Angewandte Limnologie Verhandlungen. Dezember; 252: 1031-1034.
Porras,  R. J. V., Bataller, E., Murgui, M. T., Torregrosa. 1996. Trophic Structure and Community Composition of Polychaetes Inhabiting Some Sabellaria alveolata (L.) Reefs Along the Valencia Gulf Coast. Western Mediterranean Marine Ecology 17(4): 583-602.
Zaouali, J. and S. Baeten. 1983. Impact de l'eutrophisation dans la lagune de Tunis (partie nord). 2eme partie: analyse de correspondances. Rapports et Proces-Verbaux des Reunions Commission Internationale pour l'Exploration Scientifique de la Mer Mediterranee Monaco 28: 327-332.
Zibrowius, H. 1973. Serpulidae (Annelida Polychaeta) des côtes ouest de l'Afrique et des ArchipelsVoisins. MuseÌe Royal de l'Afrique Centrale (Tervuren). Annales. SeÌrie in 8, 207:1-93.
Zibrowius, H. 1978. Quelques recoltes de Serpulidae (Annelida Polychaeta) sur les cotes nord de laTunisie. Bulletin de l'Office National des Peches Republique Tunisienne, 2: 221-222.
Zibrowius, H., and C. H. Thorp 1989. A review of the alien serpulid and spirorbid polychaetes in the British Isles.  Cahier Biologie Marine, 30: 271-285.
Honeycomb worm – Sabellaria alveolata – General information. MarLIN website. Available at: http://www.marlin.ac.uk/speciesfullreview.php?speciesID=4277 (Accessed: 18/12/15),

Criterion A Text:
There is insufficient information on past and any future trends on this habitat. Therefore, the habitat type is assessed as Data Deficient under Criterion A.

Criterion B Text:
The habitat is widespread in the Eastern and Western Mediterranean and the EOO is larger than 50,000km2. AOO is less than 50. There is a lack of information to determine trends in the spatial extent or the biotic and abiotic quality, on whether a threatening process will likely cause continuing declines or exists at very few locations. Therefore it exceed the thresholds for a threatened Category and is assessed as Data Deficient under Criterion B1 and B3.
The AOO suggests this habitat could be Endangered under criterion B however given the lack of information on its trends in quantity and quality and the fact that its overall distribution is unknown, and the AOO presented here is likely to be an underestimate, expert opinion is this habitat should also be considered Data Deficient under criteria B2.

Criterion C/D Text:
The assessment of reduction in abiotic and/or biotic quality is not possible due to the lack of studies and data on past state conditions especially regarding Sabellaria reefs. It is likely that changes along seashore due to the habitat change and exploitation, illegal buildings and development of transport systems, have highly modified the sedimentary condition that influence Sabellaria reef development. However, at present it is not possible to quantify this impact. Moreover, considering that the main builder species living in very shallow areas potentially subjected to ocean acidification and  surface sea water warming, global climate changes could have particularly severe effect on their development, also considering the introduction of alien species, causing overgrowing of algae in the biological structures. 
As it is not possible to calculate the reductions in abiotic and/or biotic quality, the habitat type is assessed as Data Deficient under Criterion C/D.

Synthesis:
At present, the knowledge of Mediterranean worm reefs in the infralittoral is too fragmentary, with little information about extent of occurrence or its area of occupancy. There have been no quantitative analysis to determine their current conservation status and to define their dynamics, in order to evaluate threats and impacts and to highlight the conservation needs or suggest management measures and protection actions. As a result, there is insufficient data to properly assess the habitat against any of the red list criteria, and the Mediterranean Polychaete worm reefs are listed as Data Deficient for both EU 28 and EU 28+.


Habitat Type Name:
A4.27. Communities of Mediterranean lower circalittoral rock

Habitat Description:
This habitat is composed of hard substrata in areas with low hydrodynamics. It typically occurs on the edge of the continental shelf, on the rocks near the break of the slope and in some areas after the shelfbreak. Because of the depth,  macroscopic vegetation is absent. This is the assemblage of the lower circalittoral zone, which characterises the Mediterranean rocky reef, also linking the circalittoral coralligenous and the bathyal habitats.
The characteristic and dominant element of the biotic community of this habitat is represented mainly by erect large sponges such as Poecillastra compressa, Phakellia ventilabrum, Tylodesma inornata, and Haliclona (Halichoclona) magna, yellow cup coral Dendrophylia cornigera, the black corals Antipatharia sp (Parantiathes larix, Antipathella subpinnata), and the brachiopodes Cistella cuneate, Gryphus vitreus and Mergerlia truncata.
Indicators of quality:
Standard biotic and abiotic indicators have been used to describe marine habitat quality. Both biotic and abiotic indicators have been used to describe marine habitat quality. These include the presence of particular species, water quality parameters, levels of exposure to a particular exposure as well as more integrated indices which describe habitat function and structure, such as trophic index, or successful stages of development in habitats that have a natural cycle of change over time.
There are no known commonly agreed indicators of quality for this habitat, although particular parameters may be set in certain situations, e.g. protected features with Natura 2000 sites, where reference values may have been determined and applied on a location-specific basis. 
Characteristic species:
Although other species are also found in relatively abundance in this habitat type, the most characteristic ones in this circalittoral lower habitat are the following:
Sponges: Tylodesma inornata, Acanthella acuta, Axinella polypoides, A. damicornis, A. verrucosa, Petrosia ficiformis, Petrosia dura, Suberites carnosus and one of the biggest and probably long-living and fragile species, Haliclona (Halichoclona) magna.
Cnidarians: Corallium rubrum, Viminella flagellum, Ellisella paraplexauroides, Paramuricea clavata, Paramuricea macrospina, Callogorgia  verticillata, Acanthogorgia hirsuta, Villogorgia bebrycoides, Muriceides lepida,  Chironephthya mediterranea, Alcyonium acaule and Paralcyonium spinulosum.
Bryozoans: Porella cervicornis.
Regarding mobile fauna, several species can be found, including many echinoderms such as Cidaris cidaris, Ophiacantha setosa, Echinaster sepositus, Echinus melo, Holothuria forskali and Antedon mediterranea; the Crustacean Decapoda Munida rugosa and the lobster Palinurus elephas as well as P. mauritanicus.

Classification:
EUNIS (v1405):
Level 4. A sub-habitat of A4.2 Circalittoral rock and other hard substrata
 
Annex 1:
1170 Reefs
 
MAES.
Shelf
 
MSFD:
Shelf sublittoral rock and biogenic reef  
 
Barcelona Convention:
IV.3.3. Community of the shelf-edge rock (Open-sea rocks – OR)

Justification Outstanding Example of Biogeographical Region:
The habitat contains different endemic species from the Mediterranean that are part of the structural community of this habitat.

Map Description:
This map has been generated using data from IUCN and EMODNET (2010). EOO and AOO have been calculated on the available data presented in this map however these should be treated with caution as expert opinion is that this may not indicate the full distribution of the habitat.

Trends in Quantity:
The extent of this whole habitat is still poorly known, and the few studies conducted recently have mostly focused on the description of the benthic assemblages. Therefore, the average current trend in quantity of this habitat type is unknown.

Trends in Quality:
A reduction of habitat quality can be inferred based on the disappearance of three-dimensional black coral forests, other structural anthozoans and erect massive sponges which result in the loss of its associated biodiversity. For instance, studies conducted in the eastern Mediterranean show the direct link between the coral abundance (e.g. Leiopathes glaberrima) and fish richness, with a decline in species of the latter as the population of the former is decreased.
ROV surveys conducted on the known black coral forests of the Mediterranean (in circalittoral and deeper rocky areas) and by-catch data from the literature estimate a decline of one third of the populations of L. glaberrima in the last 30 years, as well as a population reduction of Antipathella subpinnata and Antipathes dichotoma of around 20%. Nonetheless, the declining populations of these species are also present at deeper habitats.
The overall current trend in quality for the EU 28 is assumed to be decreasing on the basis of the information above, while it remains unknown for the EU 28+.

% of Distribution of the Habitat Type within the EU 28:
The habitat is widely present in the Mediterranean Sea in both EU 28 and EU 28+ countries. An estimation of its percentage distribution within the EU 28 is unavailable until more accurate estimates of its distribution is provided.

Justification of Restricted Area:
The habitat is widespread along the Mediterranean coast and the EOO exceeds 50,000km2.

Pressures and Threats:
Few studies have been dedicated to the impact of demersal fishing activities on circalittoral hard-bottom communities, especially in the Mediterranean basin. Long lining, however, is generally practiced in these untrawlable areas and is being reported to impact black corals (Antipatharia species) which are part of the communities that shape this habitat. The most significant damage of this type of fishing is the mechanical damage of the colonies, their smothering by the resuspension of nearby soft sediments. Damaged colonies are also more susceptible to the colonisation of epibiont organisms that slowly increase their mortality. Signs of trawling activities on these habitats with silt bottoms (e.g. Bourcard Canyon) have also been seen by ROV (Medseacan campaign).
Corallium rubrum is still collected illegally using dredging devices such as the Saint Andrew cross, breaking and entangling the coral and causing massive habitat destruction. Black corals have also been commercially exploited for jewelery for centuries, and Mediterranean fishing (trawling, gill net, bottom longlines and traditional recreational fishing gears) has been reported in the past from  France, Cyprus, Croatia and Malta.
Sea floor drilling activities for oil exploration, land pollution, sedimentation and thermal anomalies have also been indicated as potential threats to the communities of this habitat.

Conservation and Management:
Basic knowledge on the habitat and its distribution in the Mediterranean, on species assemblages and biology (distribution, abundance, habitat preferences, life-cycles) and monitoring data on trends is needed to improve spatial planning in general, and strategic planning of human activities when there are competing demands in particular.
Designation of Marine Protected Areas (MPAs) and Fisheries Restricted Areas (FRAs) in sites where this habitat occurs or extension of existing ones, should be established to create a representative network of Mediterranean MPAs. This will also help monitoring and regulating the fishing effort, especially the establishment of closed areas over part of the distribution of this habitat to protect juvenile and spawning fish and fragile benthic communities.
Regulation of artisanal fishing activities, such as benthic long lines, trammel and gillnets, on rocky areas inhabited by threatened species that are the main component of this habitat should be enforced. This should be particularly encouraged where the habitat occurs near the shore (i.e. western Corsica, the Ligurian Sea) because the habitat is even more exposed and the control of fishing should be easier to manage.
Additionally, assessment for the further inclusion of massive Mediterranean sponges which are associated with this habitat, in the Annex II of the Barcelona Convention should be proposed.

Conservation Status:
Annex 1: 
1170 Reefs: MMED, XX
There are no direct conservation measures in place for this habitat but some of the associated anthozoan and sponge species are included under different international instruments.
Black corals

Capacity to Recover its Typical Character and Functionality?:
In general, capacity for recovery is unknown. It is suspected however, that the recovery from damage caused by fisheries of some of the main fauna such as D. cornigera or black corals would probably take several hundreds to thousands of years. This is due to the slow growth rate and low dispersal ability that influence the low recovery ability of some of these species. Recovery capacity for erect sponges is unknown.

Summary:
This habitat type is typical of the Mediterranan lower circalittoral rocky floor, and is mainly characterised by erect sponges, some black corals (Antipatharia sp), the yellow cup coral Dendrophylia cornigera and D. ramea and molluscs, among others. It is known that the biological structures of some species such as L. glaberrima act as a nursery area for commercial species and large predators (e.g. catsharks Scyliorhinus canicula and large groupers).
The most significant damage of this type of fishing is the mechanical damage of the colonies, their smothering by the resuspension of nearby soft sediments. Corallium rubrum is still collected illegally using dredging devices. Sea floor drilling activities for oil exploration, land pollution, sedimentation and thermal anomalies have also been indicated as potential threats to the communities of this habitat. Basic knowledge on the habitat and its distribution in the Mediterranean, on species assemblages and biology (distribution, abundance, habitat preferences, life-cycles) and monitoring data on trends is needed to improve spatial planning in general, and strategic planning of human activities when there are competing demands in particular. Designation of Marine Protected Areas (MPAs) and Fisheries Restricted Areas (FRAs)  especially the establishment of closed areas over part of the distribution of this habitat to protect juvenile and spawning fish and fragile benthic communities, regulation of artisanal fishing activities, such as benthic long lines, trammel and gillnets.

References:
Bo, M., Orejas, C., Garcia, S., Antoniadou, C. and Cerrano, C. 2015. Antipathella subpinnata. The IUCN Red List of Threatened Species 2015: e.T50902681A50902879. Downloaded on 18 January 2016.
Bo, M., Bava, S., Canese, S., Angiolillo, M., Cattaneo-Vietti, R. and Bavestrello, G. 2014. Fishing impact on deep Mediterranean rocky habitats as revealed by ROV investigation. Biological Conservation 171: 167–176 pp.
Bo, M., Bavestrello, G., Canese, S., Giusti, M., Salvati, E., Angiolillo, M. and Greco, S. 2009. Characteristics of a black coral meadow in the twilight zone of the central Mediterranean Sea. Marine Ecology Progress Series 397: 53-61 pp.
Bo, M., Canese, S. and Bavestrello, G. 2013a. Discovering Mediterranean black coral forests: Parantipathes larix (Anthozoa: Hexacorallia) in the Tuscan Archipelago, Italy.Italian Journal of Zoology DOI: 10.1080/11250003.2013.859750.
Cau, A., Follesa, M. C., Bo, M., Canese, S., Bellodi, A., Cannas, R.  and Cau, A., 2014.  Leiopathes glaberrima forest from South West Sardinia: a thousand years old nursery area for the small spotted catshark Scyliorinus canicula. Rapport Commission International Mer Mediterranee, Marseilles. 2014, p 40.
Canese, S. and Bava, S. 2014. The Decline of top predators in deep coral reefs. UNEP/MAP – RAC/SPA, Proceedings of the 1st Mediterranean Symposium on the conservation of Dark Habitats, Tunis, 2014, pp. 31 - 36 (atti di: 1st Mediterranean Symposium on the conservation of Dark Habitats, PortoroÅ¾, Slovenia, 31 October 2014).
Ifremer, 2011. Description et cartographie des biocénoses rencontrées au cours de la campagne MEDSEACAN (Aamp/Comex). By Pedel Laura, Fabri Marie-Claire, RST.ODE/LER-PAC/11-11.
Gili, J. M., Madurell, T., Requena, S., Orejas, C., Gori, A., Purroy, A., Domínguez, C., Lo Iacono, C., Isla, E., Lozoya, J. P., Carboneras, C., Grinyó, J. and Sardá, R. 2011. Caracterización física y ecológica del área marina del Cap de Creus. Informe final área LIFE+INDEMARES (LIFE07/NAT/E/000732). In: Fundación Biodiversidad (ed.). Instituto de Ciencias del Mar/CSIC (Barcelona), Madrid.
Mytilineou, C., Smith, C. J., Anastasopoulou, A., Papadopoulou, K. N., Christidis, G., Bekas, P., Kavadas, S. and Dokos, J. 2014. New cold-water coral occurrences in the Eastern Ionian Sea: Results from experimental long line fishing. Deep Sea Research Part II: Topical Studies in Oceanography 99: 146-157 pp.
Orejas, C., Bo, M., Bavestrello, G., Antoniadou, C. and Garcia, S. 2015. Dendrophyllia cornigera. The IUCN Red List of Threatened Species 2015: e.T50160903A51216323. Downloaded on 18 January 2016.
Vacelet, J. 1969. Eponges de la Roche du Large et de l'étage bathyal de Méditerranée (Récoltes de la soucoupe plongeante Cousteau et dragages). Mémoires du Muséum national d'Histoire naturelle, (A, Zoologie), 59, 2, 145–219, pls I–IV.

Criterion A Text:
There is no information on any past trends for this habitat type and insufficient data to predict future trends in quantity. This habitat has therefore been assessed as Data Deficient under criterion A for both the EU 28 and EU 28+.

Criterion B Text:
The habitat is present in the eastern and western Mediterranean Sea. EOO and AOO values exceed the thresholds for a threatened category. However, there is no information available on whether there is a continuing decline in the spatial extent or the biotic and abiotic quality, on whether a threatening process will likely cause continuing declines, and on the number of locations. This habitat has therefore been assessed as Data Deficient under criteria B for both the EU 28 and EU 28+.

Criterion C/D Text:
There is insufficient data from many Mediterranean regions to ascertain the degree of reduction in the abiotic and/or biotic quality of the habitat. Therefore, the habitat type is assessed as Data Deficient under Criterion C/D1.

Synthesis:
This is a very poorly studied habitat type that hosts several endangered species. There are only a few reports of its distribution with a description of the composing communities along some EU Mediterranean countries and almost none from non-EU countries. The scarcity of the information across the Mediterranean means it has not been possible to determne if a reduction in the quality of the habitat is widespread and the is no quantifiable data on quality. This habitat has therefore been assessed as Data Deficient for both EU 28 and the EU 28+.

Assessors:
Otero, M. M., Pietro Canese, S., Fourt, M., Tunesi, L. and Bo, M.


Habitat Type Name:
C5.4 Inland saline or brackish helophyte bed

Habitat Description:
This habitat includes helophytes beds developing in inland saline or brackish lakes, ponds and other standing or slowly flowing waters (such as saline Mediterranean rivers) subjected to dry out during summer. The habitat may include, depending by the hydrological regime, emergent communities dominated by species tolerant to brackish or saline conditions such as Bolboschoenus maritimus, Typha laxmannii, Typha domingensis, Phragmites australis, Schoenoplectus tabernaemontani, Schoenoplectus triqueter, or communities dominated by tall rushes, such as Juncus maritimus, Juncus acutus and Juncus subulatus. The communities are species-poor and often mono-dominant. Similar communities in dune slacks are considered part of habitats B1.8a or B1.8b.
In warmer and continental parts of Europe, during the hot summer, the water level in the wetlands may decrease and the water may even completely disappear. Several species inhabiting this habitat, especially reed, may survive even under such hypersaline conditions. Bolboschoenus maritimus is the most widespread middle tall helophyte on the water margins of wetlands with different levels of salinity, growing in a range from freshwater to hypersaline water. These communities mainly inhabit the water fringes, but when a wetland dries out during the year, they may expand and cover the whole bottom of a lake or pond.
This habitat is typically in contact with the habitats C1.5 (Permanent inland saline and brackish waters), C3.5 (Periodically exposed saline shores with pioneer and ephemeral vegetation) and E6 (inland salt steppes). It is distributed in the arid continental and Mediterranean parts of Europe.
Indicators of quality:
Minimum salinity around 0.5 ‰
Natural high electrical conductivity of the water
No alteration of the natural salinity range
Dominance of halophytic emergent species rather than freshwater emergent species
Absence of overgrowing with shrubs and trees
No signs of eutrophication and dominance of ruderal species
No indicator of negative anthropogenic influence (e.g. regulation of the water level, chemical pollution)

Characteristic species:
Flora:
Vascular plants: Aster tripolium, Bolboschoenus maritimus, Carex melanostachya., Carex extensa, Carex distachya, Cirsium brachycephalum, Juncus acutus, Juncus gerardii, Juncus maritimus, Juncus subulatus, Lotus tenuis, Melilotus dentatus, Mentha pulegium, Phalaris arundinacea, Phragmites australis, Puccinellia distans, Puccinellia limosa, Puccinellia peisonis, Schoenoplectus litoralis, Schoenoplectus pungens, Schoenoplectus tabernaemontani, Schoenoplectus triqueter, Scorzonera parviflora, Typha domingensis, Tripolium pannonicum, Typha laxmannii
Fauna:
Invertebrates: Lestes macrostigma, Scirpophaga praelata
Vertebrates: wintering ducks (e.g. Anas crecca, Anas acuta, Ana platyrhynchos, Netta rufina), Anser anser, wintering and migrating waders (e.g. Gallinago gallinago, Himantopus himantopus), Rallidae

Classification:
EUNIS:
C3.1 Species-rich helophyte bed
C3.2 Water-fringing reedbeds and tall helophytes other than canes
Annex 1:
1340* Inland salt meadows (small part)
EuroVegChecklist:
Scirpion maritimi Dahl et Hadac 1941
Phragmition communis W. Koch 1926
Typhion laxmannii Losev et Golub in Golub et al. 1991
Meliloto dentati-Bolboschoenion maritimi Hroudová et al. 2009
Juncion maritimi Br.-Bl. ex HorvatiÄ‡ 1934

Emerald:
-
MAES-2:
Wetlands
IUCN: 
5.14 Permanent saline, brackish or alkaline lakes
5.15 Seasonal, intermittent saline, brackish or alkaline lakes and flats
5.16 Permanent saline, brackish or alkaline marshes and pools
5.17 Seasonal, intermittent saline, brackish or alkaline marshes and pools

Justification Outstanding Example of Biogeographical Region:
The habitat, although fragmented, is typical of shallow, temporary saline or brackish waters which are distributed over a large area in Europe and elsewhere.

Map Description:
Map is incomplete with many data gaps, but the range is relatively well indicated. Data sources: ART17, EVA, EXP, LIT, NAT.

Trends in Quantity:
Recent trends, estimated based on 6 EU28 countries are -14,2% over the last 50 years (-14,5% for 7 EU28+ countries). Actually, the trends reported by 5 EU28 countries average -42,7%, while Austria reported a 45% increase for its area which accounts for 33% of the EU28 area. Historical trends for 3 EU28 countries calculated over a 133-230 yr period reveal a -87% decrease for an initial area of 2035 sq. km (-87% for 4 EU28+ countries for an initial area of 2044 sq km). Future trends are expected to decrease according to 6 experts (from -5 to -20%), to remain stable (Lithuania) our to increase (Austria), providing a mean quantitative estimate of -16,8%.

Trends in Quality:
Extent of degradation over the last 50 years is estimated at 34% with a severity of 48% based on 4 EU28 and 5 EU28+ countries. Current trends are considered as decreasing (7 countries) or stable (5 countries). Very few experts have opinion about future trends (only one, expected decrease) and two reported historical decrease.

% of Distribution of the Habitat Type within the EU 28:
About 20%, assuming the habitat to be restricted to Eurasia and considering the slightly more restricted distribution of some of the typical species.

Justification of Small Range/Regression:
The habitat is sparsely distributed over an area of more than 50 000 km2 and has been either decreasing, stable or increasing over recent times.

Justification of Restricted Area:
As many wetlands, this habitat occupies typically small areas colonising parts of shallow lakes, ponds and rivers subjected to to dry out during summer.

Pressures and Threats:
Land reclamation for expansion of agricultural and urban areas are probably responsible for most of the historical decline in inland saline or brackish helophyte beds in europe. Declines over the last decades are mostly associated with human induced changes in hydraulic conditions: modification of catchment areas or changes in water allocation will translate into reduced hydroperiod leading potentially to more terrestrial vegetation, while input of freshwater to serve human uses such as waterfowl hunting or ecotourism in dry areas will translate into increased flooding and decreased salinity favouring tall helophyte dominated vegetation.

Conservation and Management:
Avoid input of freshwater that would modify water (soil) salinity and prevent seasonal dry periods. Avoid embankment, modification of cathment area or water derivation that would result in absence of flooding (which can be corrected by water input in some areas). From a broader nature conservation point-of-view tall helophytes may form a threat to more endangered saline or brackish grasslands. Therefore extensive grazing should be promoted where tall helophytes are at risk of expansion.

Conservation Status:
In some inland sites the habitat type may be considered as a small part of Annex 1-type 1340. Also some sites may have been considered under 1410, but 1410 relates to coastal habitats.

Capacity to Recover its Typical Character and Functionality?:
Yes, if adequate water levels/hydroperiods or shores can be restored. Pending on the situation, this can be done through indirect intervention (eg improving catchment area functionality) or naturally (by stopping water input).

Summary:
This habitat includes helophyte beds developing in and around inland saline or brackish lakes, ponds and other standing or slowly flowing waters such as saline Mediterranean rivers that are subject to summer drying. The habitat may include, depending on the particular hydrological regime, emergent communities dominated by a variety of tall or tussocky species tolerant of brackish or saline conditions. Distributed in both the continental part of Europe and the arid Mediterranean region, where it can dry out completely in the summer and become hyper-saline. Threats include land reclamation for agricultural and urban expansion, anthropogenic changes in hydrology, input of freshwater to serve waterfowl hunting or ecotourism in dry areas. Safeguarding the distinctive hydrology and controlling spread of helophytes by grazing are the main conservation actions.

References:
Hroudová, Z., Hrivnák, R., Chytrý, M. 2009. Classification of inland Bolboschoenus-dominated vegetation in Central Europe. Phytocoenologia 39:205-215.

Criterion A Text:
The estimated reduction in quantity over the last 50 years is calculated based on territorial data of 6 EU28 countries and one additional EU28+ country, leading to an average value of -14.2% for EU28 and-14.5% for EU28+. In fact, the trend reported by 5 EU28 countries averages -42,7%, while Austria reported a 45% increase for its area which accounts for 33% of the EU28 area. Historical trends for 3 EU28 countries calculated over a 133-230 year period reveal a -72% decrease for an initial area of 2035 sq. km2. Also here Austria reported an increase, which is overruled by large decreases in Hungary and the Czech Republic.

Criterion B Text:
The EOO, AOO and number of locations of the habitat are larger than the thresholds for criterion B.

Criterion C/D Text:
Degradation in quality over the last 50 years is estimated to have affected about 31% of the area with a severity of 38%, based on data from 6 EU28 and 1 EU28+ countries. Current trends are considered as decreasing (7 countries) or stable (5 countries). Very few experts have data on future trends and only two countries reported quantitative values for historical decrease.

Synthesis:
Saline reedbeds qualify as Endangered (EN) due to a very large historical decline in quantity (72%) based on estimations from three EU28 and one addiitonal EU28+ countries. Although the number of countries is low, the analysed area is still more than 50% of the present area. The most severe historical decline took place in Hungary (-90%) and the Czech Republic (-98%). These values overrule a strong historical increase in Austria.

Contributors:
Habitat definition: R. Tzonev
Territorial data: S. Armiraglio, S. Assini, G. Buffa, A. ÄŒarni, P. Finck, N. Juvan, A. Mikolajczak, Z. Molnár. D. Paternoster, V. RašomaviÄius, U. Raths, U. Riecken, J. Šibík, A. Ssymank, K. Šumberová, R. Tzonev, D. Viciani, E. Weeda
Working Group Freshwater Habitats: G. Arts, F. Landucci, J.A. Molina, B. Poulin, H. Toivonen


Habitat Description:
Xerophytic shrub communities of Mediterranean nano-phanerophytes with rolled or densely hairy leaves, rich in aromatic compoundsdominated by Cistaceae, Labiatae and sometimes by spiny brooms (Genista spp. ) that are always seral stages of forests or high-scrubs (mostly Quercetea ilicis); distributed from the thermo- to the lower supra- mediterranean vegetation belts with semi-arid to subhumid bioclimatic conditions, always in acidic, silicate-derived soils, excluding ultramafic substrata  with alkaline reaction. These communities occur on shallow,  frequently eroded soils with very acidic raw organic matter (mor type humus) throughout the Western Mediterranean subregion. Their range  has been expanded  due to human disturbances, namely the destruction of woodlands, and subsequent burning, grazing and agriculture. After abandonment of agricultural fields, after burning or after management of forest landscapes in Mediterranean bioclimates these communities act primarily as pioneer woody vegetation, being composed mostly of R-strategists, partly summer-deciduous seeder shrubs, which are also radiation-prone (heliophilous). As long as the disturbance regimes are kept (fire, tilling) shrub encroachment  might  occur and successional processes halt at the garrigue stage for a long time; hence  the garrigues may have a quasi-permanent character. Garrigues are characterized by high taxa diversity and also a great bio-coenotical and biogeographical differentiation, harboring many endemics. There are two main groups of communities following the  nature of the substratum: those on hard silicate (Lavanduletalia stoechadis) rocks and those  on loose-sand dunes and palaeodunes (Stauracantho-Halimietalia commutati). Several subtypes (alliances) may be recognized according to biogeography in the span of western Mediterranean region of Europe:
1. Cistion ladaniferi: garrigues of Cistus spp. and Lavandula stoechas at the thermo- to the supra- mediterranenan oceanic bioclimatic belts distributed to the north-central-Levantine Iberia, south coast of France, up to  Italy to  the coast of Liguria.
2. Cistion laurifolii: garrigues dominated by Cistus laurifolius and Lavandula pedunculata s.l. at the meso- to supra-mediterranean semi-continental bioclimatic belts distributed to  west-central Iberian..
3. Ulici argentei-Cistion ladaniferi: garrigues dominated by Cistus ladanifer and C. monspeliensis and co-dominated by Lavandula sampaioana (various subsp.), L. luisieri, Genista hirsuta, Ulex borgiae, U.eriocladus, U. argenteus distributed to central south-western Iberian (luso-estremadurensian and betic provinces).
4. Calicotomo villosae-Genistion tyrrhenae: Italo-Thyrrenean garrigues on  volcanic substrata at  the thermos-mediterranean belt, dominated by Genista tyrrhena, G. cilentina, Erica multiflora, Cistus spp.., Calicotome villosa, Ampelodesmos mauritanica.
5. Teucrion mari: garrigues dominated by Teucrium marum, Stachys glutinosa, Cistus creticus, Phagnalon rupestre subsp. annoticum, Helychrysum italicum subsp. microphyllum, Genista corsica, G. sardoa, G. ephedroides, G. sulcitana, Santolina insularis, Euphorbia cupanii at the meso- to thermos-mediterranean belts of Sardinia and Corsica.
6. Coremation albi: endemic-rich garrigues communities dominated by Stauracanthus genistoides (= S. lusitanicus), S. spectabilis, Halimium halimifolium, H. calycinum, Ulex australis subsp. australis and U. australis subsp. welwitschianus, U. argenteus subsp. subsericeus, Thymus camphoratus, Thymus capitellatus, Thymus albicans subsp. donyanae  on consolidated dunes and palaeodunes distributed from the Portuguese coasts to the coasts of Andalusia. This subtype is characterized by the following genera  with endemic species:  Armeria, Dianthus, Thymus, Avenula and Sideritis (see flora).
Note on the circumscription of the habitat
Due to vagueness and broadness of the historical ‘garrigue’ concept, the circumscription of the habitat F6.1b should become  more precise. Thus, we circumscribe the habitat F6.1b to contain typical nano-phaneropytic (dwarf scrub) garrigues, seral of forests, on acidic silicate-derived soils, excluding chamaephytic mountain vegetation and sea-cliff vegetation. Taking Mucina et al. [EuroVegChecklist] (ined.) as syntaxonomic reference, the habitat includes the major part of the Cisto-Lavanduletea stoechadis vegetation class; hence, the following units or syntaxa with physiognomic and ecological  affinities to Cisto-Lavanduletea are excluded: chamaephytic cushion scrub vegetation of Corsica Sardinia and Sicily occurring at the  upper supra- to mountain- and oro- mediterranean belts assigned to Carici-Genistetea lobelii and Rumici-Astragaletea siculi - only on Mount Etna) is excluded (F7.4b); Armerio sardoae- Genistion salzmanii is excluded (considered Carici-Genistetea lobelii); tall-broom (Genistetea) communities seral of forests are excluded (F3.1c Cytisetea scopario-striati); xerophytic cushion chamaephytic scrub under the influence of salty wind is excluded (F7.1-2 or B3.1-3b: Helichrysetalia italici, Crithmo-Staticetea or Rosmarinetea); Staehlino-Ulicion baetici is excluded due to ultramafic siliceous alkaline substrata (F6.1a Rosmarinetea officinalis); Teucrion mari and Calicotomo villosae-Genistion tyrrhenae are considered separate alliances and are included in F6.1b; any type of vegetation of F5.1/2 (Pistacio-Rhamnetalia alaterni, Quercetea ilicis), namely Quercion fruticosae is excluded. All Cisto-Micromerietea vegetation from the Eastern Mediterranean subregion is excluded, due to strict biogeographic circumscription of the habitat to the Western Mediterranean ; thus, only territories west of Italy, including the Thyrrenian coast, Sicily, Corsica, Sardinia, Malta and the Baleares are included  ( the Adriatic coasts of Italy and territories eastwards are not included). All heathland habitats (F4.2) are excluded. Erica multiflora communities on limestone, even if decarbonated are excluded (Cisto eriocephali-Ericion multiflorae, Cisto-Micromerietea or Rosmarino-Ericion multiflorae, Rosmarinetea). Those communities including E. multiflora on substrata other than limestone are included. Semi- nitrogen or salt prone shrub vegetation is also excluded (F6.8a - Pegano-Salsoletea class).
Indicators of good quality:
As acidic garrigues are considered seral vegetation stages of woodlands, their maintenance in the landscape mosaic depends on the persistence of disturbance: cutting, fire, grazing and agricultural abandonment. Due to the pioneer character of this vegetation type, primary colonization stages after bare ground are species-poor  basal communities lacking  most specialized plants and poccessing less conservation value. Meta-stability of the garrigues stage for some time is necessary to reach coenotic saturation, i.e. defined by the presence of its full characteristic set of bio-indicators. Thus, as most garrigues follow plowing in managed forest-agricultural context, some patches are to be kept without disturbance for greater time. As much as more characteristic-indicator species are present, the greater the value of the communities.
In general, short periods between plowing should be avoided (< 15 years). In a greater time span, garrigues may be replaced by taller woody vegetation due to progressive ecological succession. The later should be taken on account when managing a landscape mosaic.
Characteristic species:
Due to the high number of species that the habitat contains as a whole, only the dominant taxa and taxa belonging to characteristic bioindicator sets at the  alliance level are listed.
Vascular plants:
Calluna vulgaris subsp. elegantissima, Cistus salviifolius, Cytinus hypocistis subsp. macranthus, Halimium viscosum, Orchis mascula subsp. olbiensis, Orchis champagneuxii, Orchis picta, Cistus crispus, Cistus ladanifer, Cistus monspeliensis, Cistus salvifolius, Cistus populifolius, Cytinus hypocistis subsp. hypocistis, Narcisssus concolor, Narcissus triandrus subsp. palidulus, Helichrysum serotinum, Thymus mastichina, Centaurea hanryi, Dianthus multiaffinis, Hypericum australe, Lavandula stoechas, Calicotome spinosa, Cytisus catalaunicus, Genista pillosa, Thymus vulgaris, Arctostaphylos uva-ursi var. crassifolia, Aster aragonensis, Cistus laurifolius, Lavandula pedunculata, Lotus corniculatus subsp. carpetanus, Thymus leptophyllus, Erophaca baetica (=Astragalus lusitanicus), Centaurea sagredoi, Centaurea tartesiana, Genista hirsute subsp. hirsute, Lavandula stoechas subsp. luisieri, Lavandula sampaioana subsp. sampaiona, Lithodora prostrate subsp. lusitanica, Sideritis lacaitae, Sideritis marianica, Sideritis paulii, Thymelaea lythroides, Ulex argenteus, Ulex borgiae, Ulex eriocladus. Genista polyanthus, Thymus camphoratus subsp. congestus, Ulex airensis, Genista tyrrhena, Genista cilentina,Genista aspalathoides, Genista demarcoi, G. desoliana, Genista gasparrini, Teucrium marum, Stachys glutinosa, Helichrysum italicum subsp. microphyllum, Phagnalon rupestre subsp. annoticum, Genista Corsica, Genista sardoa, Genista ephedroides, Genista sulcitana, Santolina insularis, Euphorbia cupanii, Armeria macrophyll, Armeria pinifolia, Armeria rouyana, Armeria velutina, Cistus libanotis, Dianthus broteri subsp. hinoxianus, Fritillaria lusitanica subsp. stenophylla, Halimium calycinum, Halimium halimifolium subsp. halimifolium, Halimium halimifolium subsp. multiflorum, Halimium verticillatum, Iberis linifolia subsp.welwitschii, Lavandula sampaioana subsp. lusitanica, Stauracanthus genistoides, Stauracanthus spectabilis subsp. spectabilis, Stauracanthus genistoides subsp. vicentinus, Thymus albicans subsp. albicans, Thymus albicans subsp. donyanae, Thymus camphorates subsp. camphoratus, Thymus capitellatus, Ulex australis subsp. australis, Ulex australis subsp. welwitschianus, Ulex aregenteus subsp. subsericeus, Helichrisum picardii var. virescens, Avenula hackelli, Klasea algarviensis, Sideritis perezlarae.

Classification:
EUNIS
F6.1 Western garrigues
EuroVegChecklist
Cistion laurifolii
Ulici argentei-Cistion ladaniferi
Cistion ladaniferi
Calicotomo villosae-Genistion tyrrheneae
Teucrion mari
Coremation albi
Annex 1:
- (in dunes similar plant communities are included under 2260)
Emerald:
-
MAES-2:
Heathland and shrub
IUCN:
3.8 Mediterranean-type Shrubby Vegetation

Justification Outstanding Example of Biogeographical Region:
This type of vegetation is exclusive of  the Western Mediterranean Subregion of the Mediterranean Region under Mediterranean macrobioclimate.

Map Description:
The map is rather complete except for the distribution in Portugal. Data source: NAT, EVA.

Trends in Quantity:
Portugal reports a great increase (+83%) in the 50-years’ time span, due to the marginal agricultural land that remained fallow (EU CAP) in an extensive way to the country. By contrast, both Spain and Italy report slight decrease in the extent of the habitat, although the habitat in Spain is covering more extensive  areas (estimated by territorial experts and not area calculated by data and information on the last 50 years period). Territorial data from France are unavailable. As a result, the average trend is -0,7% decrease, which means practically stable condition for the whole EU28 (and EU28+) distribution range of the habitat.

Trends in Quality:
Using available territorial data, the % extent of degradation (with slight severity in all countries) is negligible (1,6 %). Thus, we consider the European global trend in quality as stable.

% of Distribution of the Habitat Type within the EU 28:
The habitat is distributed in both European and North African areas of the Western Mediterranean subregion. In Europe, the habitat stretches from Portugal to the Thyreenean coast of Italy. Along the North African coast, its range is from the Tingitanian peninsula (Tanger, Morroco) in the west, includes the subcoastal areas of Algeria and Tunisia and reaches, in the east, the Cyrenaica peninsula in Lybia (Al Akhdar). We estimate that approximately 50% of the habitat is within the EU28 and the remaining 50% is in North Africa.

Justification of Small Range/Regression:
The habitat does not have a small range, since the EOO is >50.000 Km2 and AOO is >> 50 grid cells (of 10x10 km2).

Justification of Restricted Area:
The distribution range of the habitat is extensive throughout the whole Western Mediterranean subregion.

Pressures and Threats:
The habitat develops mostly after agricultural abandonment or after very long fallow intervals. Agricultural intensification, changes in the agriculture system (such as change in crops, intensification by fertilization or reduction of fallow period, introduction of grazing in large areas, afforestation with exotic alien species), are liable to induce reductions in quantity and quality of acidic garrigues. The removal of undergrowth in parklands (dehesa/montado systems) might also be locally important in order to safeguard the succession of old garrigues. Many acidic garrigues are fire-prone, i.e. composed of pyrophytes. Measures preventing wildfires might also reduce the extent of the acidic garrigues. Natural succession towards forest or pre-forest stages might reduce the area of acidic garrigues. The start of widespread use of machines to agriculture in the decades of 50’s and 60’s might have caused reduction in the extent of the acidic garrigues. However, in our days, none of these effects is significant to be considered a threat for the habitat.

Conservation and Management:
Although in most part of the habitat area no special management measures are required, other than regular plowing (when included in very extensive agro-silvo-pastoral systems), the reduction of the period between plowing due to intensification or preventing fires, might not allow succession to go beyond the species poor pioneer stages. Thus, in some areas where conservation of garrigues is desirable (also as habitat for wildlife), an extension in period between plowing might be advisable to allow succession towards a species saturated condition. As to the specific case of palaeodune scrub (cf. 2260 Annex 1) it is advisable that tilling is kept at a minimum and only when, by sucession, the pre-forest stages tend to become dominant at local scale.

Capacity to Recover its Typical Character and Functionality?:
In general, no interventions are needed to promote the habitat’s distribution and support its recovery.It is composed of pioneer species colonizing soils after cessation of agricultural activities. The establishment of species saturated condition is reached in about 10 years.

Summary:
Western acidic garrigue comprises pioneer scrub vegetation dominated by xerophytic dwarf shrubs and herbs established between fallow periods or after abandonment in the traditional agricultural landscapes of the western Mediterranean. It occurs on thin, often eroded, acid humic soils derived from siliceous bedrocks or on dune sands and the associated vegetation is very diverse according to the regional climate and terrain. As the habitat is seral, its persistence depends on the maintenance of disturbance by fire, grazing and periodic fallow and it is threatened by lack of fire, agricultural improvement and permanent abandonment.

References:
Bardat, J. etal. 2004. Podrome des végétations de France. MNHN. 171 pp.
Biondi, E. & Blasi, C. 2014. Podromo della vegetazione d’ Italia. Check-list sintassonomica aggiornata di classi, ordini e alleanze presenti in Italia. http://www.prodromo-vegetazione-italia.org/ [accessed 08.10.14].
Costa, J.C., et al. 2012. Vascular Plant Communities in Portugal (continental, Azores & Madeira) Global Geobotany 2: 1 -180.
Mucina, L. et al. 2014. Vegetation of Europe: hierarchical classification system of vascular plant, bryophyte, lichen and algal communities. [ined.]
Rivas-Martínez, S. 2011. Mapa de séries, geoséries y geopermaséries de vegetación de España.  Parte II Itinera Geobotanica 18(1): 5-425.
Rivas-Martínez, S. 1979. Brezales y jarales de Europa occidental (revisión fitosociológica de las classes Calluno-Ulicetea y Cisto-Lavanduletea) Lazaroa 1:

Criterion A Text:
For all A-type criteria, as well as for future prospects of the habitat, a stable condition is expected. A historical (A3) increase of unknown importance is also postulated by assessors.

Criterion B Text:
Both EOO and AOO are much greater than the thresholds 50.000 Km2 and 50 grid cells (of 10 x 10 km2).

Criterion C/D Text:
There is a negligible average european trend in quality reduction.

Synthesis:
The habitat is assessed as Least Concern (LC) based on available territorial data. The habitat has not a small range and has not suffered any historical reduction in quality or quantity. A stable condition and no important threats are expected in the future. This is in consistency with the habitat's pioneer nature, common in former agricultural land after abandonment.

Sub-habitats in Need of Examination:
Although various sub-habitats (either based on biogeographical or ecological criteria, such as substratum, bioclimate, etc.) might be recognized along the distribution range of the habitat, its pioneer character and its high resilience rate does not re

Contributors:
Description by J.Capelo & Dalila Espírito-Santo
Territorial experts: J.Capelo, M.D. Espírito-Santo, J.A. Campos, E. Agrillo, F. Attorre, S. Bagella, L. Casella, G. Giusso Del Galdo, C. Marcenò, D. Viciani
Working Group Heathland & Scrub: M. Aronsson, F. Bioret, C. Bita-Nicolae, J. Capelo, A. ÄŒarni, P. Dimopoulos, J. Janssen, J. Loidi


Habitat Description:
Open scrub formed by stem and leaf succulents, often belonging to the Euphorbia genus (tabaibales and cardonales), and woody sclerophyllous shrubs. It develops in the xerophytic to desertic lowland areas of the Canary Islands, covering practically the whole of the area in the eastern islands (Lanzarote and Fuerteventura) and the lower belts in the rest of the archipelago, particularly in the south facing slopes. The substrata are rocky, often with very poorly developed soils (lithosols).
The succulent scrub has elements of arid tropical origin, related to habitats existing in arid territories of tropical Africa. As in the other Canarian habitats, many geovicariant endemics for each of the islands or islands groups enrich the characteristic species list. This habitat type is divided into two main subtypes, one in the lower altitude on rocky soils and dryiest areas, in which the succulent scrub is dominant, and the second, in somewhat higher elevations, moister conditions and more structured soils, dominated by a xerophytic scrub of Rhamnus and Olea, much more related to Mediterranean ecosystems and containing more Mediterranean flora elements.
This habitat has been historically used by man and altered due to goat grazing, housing, and building of urban areas. As a result, it is easily invaded by nitrophilic species of the Forsskaoleo-Rumicetalia lunariae.
Indicators of good quality:
Absence of nitrophilous and non-native species
Presence and abundance of endemic succulent shrubs

 
Characteristic species:
Flora
Vascular plants: Allagopappus dichotomus, Anagyris latifolia, Androcymbium hierrense, Argyranthemum callichryson, Argyranthemum coronopifolium, Argyranthemum escarrei, Argyranthemum gracile Argyranthemum sundingii, Asparagus arborescens, Asparagus nesiotes, Asparagus pastorianus, Asparagus ploclamoides, Asparagus scoparius, Asparagus umbellatus, Brachypodium arbuscula, Bupleurum handiense, Bupleurum salicifolium subsp. acidyphyllum, Bystropogon plumosus, Bystropogon odoratissimus, Campylanthus salsoloides, Caralluma burchardii, Ceropegia dichotoma, Ceropegia fusca, Cistus monspeliensis subsp. canariensis, Convolvulus floridus, Convolvulus lopezsocasi, Convolvulus scoparius, Dorycnium eriophtalmum, Dracaena draco, Echium aculeatum, Echium brevirame, Echium decaisnei, subsp. purpuriense, Echium giganteum, Echium strictum, Erysimum bicolor, Euphorbia aphylla, Euphorbia atropurpurea, Euphorbia balsamifera, Euphorbia berthelotii, Euphorbia canariensis, Euphorbia handiensis, Euphorbia lamarckii, Euphorbia regis-jubae, Globularia salicina, Helianthemum canarinse, Herniaria canariensis, Hypericum canariense, Jasminum odoratissimum, Juniperus turbinata subsp. canariensis, Justicia hyssopifolia, Kickxia sagittata, Kickxia scoparia, Kleinia neriifolia, Marcetella mocquiniana, Maytenus canariensis, Micromeria hyssopifolia var. hyssopifolia, Micromeria hyssopifolia var. kueglerii, Micromeria varia, Micromeria teneriffae var. cordifolia, Neochamaela pulverulenta, Olea europaea subsp. canariensis, Olea europaea subsp. cerasiformis, Pancratium canariense, Parolinia intermedia, Parolinia ornata, Paronychia canariensis, Periploca laevigata, Ploclama pendula, Reichardia famarae, Reseda scoparia, Retama raetam, Rhamnus crenulata, Rubia fruticosa subsp. melanocarpa, Rubia fruticosa subsp. fruticosa, Ruta pinnata, Rutheopsis herbanica, Scilla haemorrhiodalis, Seseli webbii, Sideritis brevicaulis, Sideritis dendrochahorra, Sideritis pumila, Spartocytisus filipes, Taeckholmia capillaries, Taeckholmia microcarpa, Taeckholmia pinnata, Tamus edulis, Teline osyrioides subsp. osyrioides, Teline osyrioides subsp. sericea, Teucrium heterophyllum, Vicia cirrhosa.

Classification:
EUNIS:
F8.1 Canary Island xerophytic scrub
F6.5 Macaronesian garrigues
Annex 1:
no relationship
EuroVegChecklist (alliances):
Aeonio-Euphorbion canariensis Sunding 1972
Euphorbion regijsjubo-lamarckii Rivas-Mart., Wildpret, O. Rodríguez et Del Arco in Rivas-Mart. et al. 2011
Retamion rhodorhizoidis Del Arco et al. 2009
Cisto canariensis-Micromerion hyssopifoliae Pérez de Paz et al. 1990 corr. Rivas-Mart. in Rivas-Mart. 2011
Emerald:
no relationship
MAES-2:
Heathland and shrub
IUCN
3.5 Subtropical/Tropical Dry Shrubland

Justification Outstanding Example of Biogeographical Region:
The habitat only occurs on the Canarian islands, part of the Macaronesian biogeographic region.

Map Description:
The map provides the complete distribution of the habitat. Data sources: NAT.
The area of the habitat according to Del Arco et al. (2010) is about 490 km2.

Trends in Quantity:
No quantitative data for the trend since 50 years have been provided in the territorial data, but an estimate can be made from figures provided by Del Arco et al. (2010); see the section Red List Assessment.

Trends in Quality:
According to the territorial data about 10% of the present habitat has decreased in quality, but no severity of decrease in quality is indicated. Some additional  and alternative estimations of decline in quality are provided in the section Red List Assessment.

Justification of Small Range/Regression:
The habitat has a restricted range, although the total EOO is slightly larger than the threshold for the criteria B. Negative trends (regression) are related to agricultural, urbanism and tourist development. The decline is ongoing and a further declin

Justification of Restricted Area:
In most sites the habitat occurs in large patches, covering large parts of the lower belts of the Canary Islands.

Pressures and Threats:
Cultivation, mixed grazing, crop production and urbanisation. Pressures from the list include construction (E01),  intensive agriculture (A06.01.01) and litter accumulation (H05.01). Development of agriculture and urban areas degrade and occupy a big part of the potential area of this habitat in the Canaries.

Conservation and Management:
The Natura 2000 network and the Canary Network of Natural Reserves cover large parts of the highest parts of the Canary Islands. A relatively low amount of the habitat F8.1 is within the boundaries of these protected areas. As regards thermo-sclerophyllous woodland, the possibilities of recovery are scarce, because of the high degree of disturbance and current use of its potential territory. Designation of protected areas should focus more on the lower areas where habitat F8.1 occurs.

Capacity to Recover its Typical Character and Functionality?:
Unknown, but in general the dominant scrubs grow relatively slow, and restoration of complete habitats is expected to last relatively long.

Summary:
This is open scrub formed by stem and leaf succulents and woody sclerophyllous shrubs that occurs in the arid and desertic locations on the Canaries. The former vegetation favours lower rocky situations, often on south-facing slopes, with rudimentary soils, the latter higher ground with more moisture and deeper soils. The vegetation is species-rich with endemics on different islands. Long histories of garzing have affected the extent and composition of the vegetation and other threats include urbanisation and tourist developments, particularly at lower levels where protected areas are less extensive.

References:
Del Arco, M.J., Wildpret, W., Pérez-de-Paz, P.L., Rodríguez-Delgado, O., Acebes, J.R., García-Gallo, A., Martín, V.E., Reyes-Betancort, J.A., Salas, M., Bermejo, J.A., González, R., Cabrera, M.V., García, S. 2006. Mapa de Vegetación de Canarias. GRAFCAN, Santa Cruz de Tenerife.
Del Arco M.J., González-González, R., Garzón-Machado, V., Pizarro-Hernández, B.,  2010.  Actual and potential natural vegetation on the Canary Islands and its conservation status. Biodiversity and Conservation 19: 3089–3140.
Rivas-Martínez, S., Widpret, W., Del Arco, M., Rodríguez, O., Pérez de Paz, P.L., García-Gallo, A., Acebes, J.R., Díaz, T.E. & Fernández-González, F. 1993. Las comunidades vegetales de la isla de Tenerife (Islas Canarias). Itinera Geobotanica 7: 169-374.

Criterion A Text:
No quantitative data for the trend since 50 years have been provided in the territorial data, but an estimate can be made from figures provided by Del Arco et al. (2010). They indicate a decline of 94% over long-historical times. This figure has been corrected for the Red List assessment, as some secondary vegetation (Euphorbia regis-jubae scrub and garrigue-like communities with Cytisus, Micromeria and Globularia) are included in the definition of the habitat type F8.1, but were not taken into account by Del Arco et al. (2010). If these scrubs are included in the calculation, the long-time historical decline is about 70%. Most of this happened in the last 500 years (estimated: 90% of the trend), and most of that in the last 50 years (estimated: 60-70% of the trend). These data result in a negative trend of about 45% in the last 50 years (leading to the category Vulnerable), and a long-historical trend (over about 500 yrs) of 63% (leading to the category Vulnerable as well). As large parts of the habitat are not under protection at present, a slight further decline may be expected in the future, but no quantitative indication is given.

Criterion B Text:
The AOO (121 grid cells) and EOO (71600 km2) of the habitat are slightly higher than the thresholds for criterion B. As the decline is ongoing and threatening processes (tourism and building impacts, pollution) are continuing as well, the habitat is assessed as near threatened (NT) under criteria B1. For B2 the AOO value is too high to meet the NT category requirements. There are no indications of few locations and events that are capable to make the habitat Critically Endangered or Collapsed in the near future, so the habitat is considered Least Concern under B3.

Criterion C/D Text:
According to the territorial data about 10% of the present habitat has decreased in quality, but no severity of decrease in quality is indicated. It is estimated however that much larger parts (50%) are negatively impacted by occurrence of non-native species (for example Opuntia, grasses) and by pollution; the impact of these processes is low however; overall the extent affected has been estimated to be 50%, and the severity 10%, which is the accumulated decline in both biotic quality (invasive species) and abiotic quality (pollution). These scores lead to a Least Concern conclusion for criterion C/D1.

Synthesis:
The overall analysis of territorial data leads to the category Vulnerable (VU) for trends in quantity over the past 50 years and long-term trends over the past 500 years. The distribution of the habitat is very limited, resulting in Near Threatened assessments for criterion B1 (restricted range extent). For trends in quality a decrease of 10% over the past 50 years has been calculated, leading to the category Near Threatened. There are indications that species of the habitat have become extinct in historical/pre-historical times.

Sub-habitats in Need of Examination:
A main division of the habitat is in two subtypes, one for the lowest and driest areas (the most threatened subtype) and one for higher, more moist sites. Besides, each of the Canary islands contains varieties with endemic species, and some of these su

Contributors:
Habitat description: J. Loidi
Territorial data: J. Loidi
Working Group Heathland & Scrub: M. Aronsson, F. Bioret, C. Bita-Nicolae, J. Capelo, A. ÄŒarni, P. Dimopoulos, J. Janssen, J. Loidi


Habitat Type Name:
F9.1 Temperate and boreal riparian scrub

Habitat Description:
This habitat includes scrub vegetation developed more permanently on unsorted gravelly deposits on the banks and shoals of turbulent seasonally-flowing streams and flood-prone rivers through the uplands of nemoral, boreal and alpine zones, as well as temporary successional willow vegetation through the European lowlands. In higher European mountains, common woody pioneers in such situations are Myricaria germanica, Salix purpurea, S. eleagnos, S. daphnoides and S. nigricans with S. phylicifolia often the leading pioneer in the Boreal zone. This kind of vegetation also extends into the Mediterranean zone of Spain where permanent flow protects streamside sediments against the seasonal drying of sediments and salinization that favours F9.3 Mediterranean riparian scrub. Here S. salvifolia, S. pedicillata and S. cantabrica are important colonisers.
These willows anchor firmly in the gravels and can tolerate further flooding, as well as browsing from wild herbivores and stock. Where accumulating gravels raise the ground surface higher above the flood, Hippophaë rhamnoides can also gain a hold, thriving in the lime-rich conditions that generally prevail here and coming to dominate in dense thickets. Such alluvial scrub, only incidentally flooded, is found both in temperate Europe and in the boreal regions. Where regular inundation ceases in the higher reaches of rivers, there can be a succession to G1.2 Riparian woodland dominated by Alnus incana.
These assemblages do not extend unchanged in composition into the lowlands of Europe and, in fact, where S. eleagnos persists along more mature riversides, it can attain the stature of a tree which excludes its stands from this habitat. However, on the sediments which are deposited by flood waters at these lower altitudes, S. purpurea can colonise with S. triandra to form willow scrub with a similar structure to that of mountain streamsides. Here, however, where the sediments stabilise, this vegetation is often a prelude to the development of G1.1 Riparian and gallery woodland dominated by S. alba and S. fragilis. However, in lowland rivers prone to repeated flooding, repeated setback of such succession can leads to re-establishment of the willow scrub.
In the boreal regions of Europe riparian scrub along rivers and mountains streams is dominated by a combination of Salix lapponum, Salix glauca, Salix lanata and Salix phylicifolia, and a herb layer of tall herbs, like Filipendula ulmaria, Geum rivale, Calamagrostis purpurea, Rumex acetosa and Comarum palustre.
Indicators of quality:
Stands of this scrub may be impermanent along very turbulent streams and rivers, developing again in the same or other places in following seasons, so discontinuity in a particular locality is not necessarily a sign of threatened quality
the maintenance of seasonal flooding fed by snow-melt or upland rains.
continuing dominance of shrubs without invading trees.
low levels of browsing by wild herbivores and stock with no decline in shrub cover.

Characteristic species:
Flora, vascular plants: Myricaria germanica, Salix cantabrica, Salix daphnoides, Salix eleagnos, Salix glauca, Salix lanata, Salix lapponum, Salix myrsinifolia, Salix nigricans, Salix pedicillata, Salix phylicifolia, Salix purpurea, Salix salvifolia Salix starkeana, Hippophaë rhamnoides.

Classification:
EUNIS:
F9.1 Riverine scrub
EuroVegChecklist (alliances):
Salicion triandrae T. Müller et Görs 1958
Rubo caesii-Amorphion fruticosae Shevchyk et Solomakha 1996
Salicion eleagno-daphnoidis (Moor 1958) Grass 1993
Salicion phylicifoliae Dierßen 1992
Salicion salvifoliae Rivas-Mart. et al. 1984
Salicion discolori-neotrichae Br.-Bl. et O. de Bolòs 1958 corr. Rivas-Mart. et al. 2002
Salicion pedicellatae Rivas-Mart. et al. 1984
Salicion cantabricae Rivas-Mart., T.E. Díaz et Penas in Rivas-Mart. et al. 2011
Annex 1:
3230 Alpine rivers and their ligneous vegetation with [Myricaria germanica]
3240 Alpine rivers and their ligneous vegetation with [Salix elaeagnos]
4080 Sub-Arctic Salix ssp. scrub
Emerald:
F9.1 Riverine scrub
MAES:
Heathland and shrub
IUCN:
3.3 Boreal shrubland
3.4 Temperate shrubland

Justification Outstanding Example of Biogeographical Region:
The habitat is spread all over Europe and occurs with some variation in all biogeographical regions. For the formal revision of EUNIS a subdivision has been proposed in two types. Of these the subtype F9.1a Arctic, boreal and alpine riparian scrub is typical for the boreal and alpine region, while the type F9.1b Temperate riparian scrub is widespread in lowland areas.

Map Description:
The map is incomplete, with data gaps throughout the range but especially in Scandinavia and distribution of Annex I type 4080 as potential occurrences. Data sources: EVA, Art17, GBIF.

Comment EU28:
Lacking data from Finland, that has a substansial part of the habitat

Trends in Quantity:
There is large variation in reported trend data between the countries. In many countries with a small area the decline is very high. On the other hand some countries with large area have a very small decline. In Scandinavia and Finland the habitat is even increasing, due to recover from fomer usage of the river shores for grazing.

Trends in Quality:
The average degradiation in quality has been calculated from terriorial data. About 20% of the area has been affected with an average severity of about 50% in EU28 and EU28+.

% of Distribution of the Habitat Type within the EU 28:
Approximately 25%. Some characteristic species of the habitat are distributed eastwards up to Siberia (Salix viminalis, S. triandra) or the Ural mountains (Salix nigricans).

Justification of Small Range/Regression:
The range is much larger than 50,000 km2.

Justification of Restricted Area:
In most sites the habitat occurs in small patches on the shores of rivers and rivlets.

Pressures and Threats:
Threats on this habitat are acting on different scale and the most drastic are damming of rivers for hydrological power plants. If the dams are large, like in northern Scandivanavia, the habitat will be totally destroyed. In other rivers the threats are more gradual, with small changes in hydrology, introduction of invasive species and changes in use of the landscape in the neighbourhood of the watercourse.

Conservation and Management:
Most important management is to restore the water regime to a level that water fluctuations are as close as possible to natural conditions. Other measures are to eradicate invasive species and to protect sites with a representative set of good examples of the habitat.

Conservation Status:
Annex I:
3230: ALP U2, CON U2, MED U1
3240: ALP U1, ATL U1, CON U1, MED U1
4080: ALP U1, ATL U2, BOR FV, CON U1

Capacity to Recover its Typical Character and Functionality?:
Restoration of watercourses may have effect in a relatively short time if the measures are robust enough. Several full scale restoration projects have been carried out, most of them with great success.

Summary:
This habitat includes scrub vegetation developed more permanently on unsorted gravelly deposits on the banks and shoals of turbulent seasonally-flowing streams and flood-prone rivers through the uplands of nemoral, boreal and alpine zones, as well as temporary successional willow vegetation through the European lowlands. Early colonists anchor firmly in the gravels and can tolerate further flooding, as well as browsing from wild herbivores and stock and other species follow as accumulating gravels raise the ground surface higher above the flood, but periodic inundation is essential. Succession itself may thus be a threat where floods cease, though a bigger threat is catchment and river management which alters the natural regime. Invasive species also need control.

References:
Pajunen, A.M., E.M. Kaarlejärvi, B.C. Forbes & R. Vitanen (2010). Compositional differentiation of willow-characterised vegetation in the western Eurasian Arctic. Journal of Vegetation Science 21: 107-119.

Criterion A Text:
The average decline in Europe was calculated from quantitative territorial data from seven countries in the EU28 and two additional countries in the EU28+. The result is a sligth decrease, not high enough to meet any threat category. The conclusion for criterion A1 is Least Concern, while for other criteria under A no data are available.

Criterion B Text:
The EOO, AOO and number of locations are much larger than the thresholds for criteria under B, leading to the conclusion Least Concern.

Criterion C/D Text:
Based on territorial data from 11 EU28 and 2 EU28+ countries the average European trends have been calculated. The figures lead to the conclusion Least Concern.

Synthesis:
There has been an overall slight decrease of the habitat in both quantity and quality over the last 50 years, but not to a degree to meet any Red List category. The situation varies a lot over Europe and the habitat is much more threathened in lowlands and the Alps compared to the Balkan and the north. In Scandinavia this willow scrub has a good quality and even shows an increase in area.

Sub-habitats in Need of Examination:
For the formal revision of EUNIS it is proposed to divide this habitat in two main types: F9.1a Arctic, boreal and alpine riparian scrub, and F9.1b Temperate riparian scrub. These two types can be clearly differentiated based on species composition, ec

Contributors:
Habitat definition: J. Rodwell
Territorial data: E. Agrillo, M. Aronsson, F. Attorre, S. Armiraglio, S. Assini, C. Bita-Nicolae, J. Bölöni, G. Buffa, A. ÄŒarni, L. Casella, M. Chytrý, R. Delarze, M. Dimitrov, P. Dimopoulos, P. Finck, H. Gardfjell, C. Giancola, D. Gigante, J. Janssen, N. Juvan, Z. KÄ…cki, K.J. Kirby, T. Kontula, J. Loidi, A. Mikolajczak, Ä. MilanoviÄ‡, F. O'Neill, D. Paternoster, G. Pezzi, V. RašomaviÄius, U. Raths, U. Riecken, J. Šibík, Z. Škvorc, A. Ssymank, D. Viciani, E. Weeda
Working Group Heathland & Scrub:  C. Bita-Nicolae, F. Bioret, A. ÄŒarni, J. Capelo, P. Dimopoulos, J.A.M. Janssen & J. Loidi


Habitat Description:
This habitat encompasses genistoid dominated high mountain scrub in the Balkan, Apennines and southern outcrops of the Alps. It can be found mainly on carbonate and ultramaphic bedrock, in places also over siliceous bedrock. The genistoid scrub (mainly dominated by Genista radiata) can reach about one meter and forms dense communities. It prefers warm-humid habitats, where fog condensates or that are exposed to precipitation, mainly steep, sunny and rocky sites with shallow soil types, where more demanding plant species cannot thrive. It often appears on sites of degraded Pinus mugo communities. Above the timberline this habitat can form the climax vegetation and mosaics with alpine pastures, Pinus mugo and Juniperus scrub. It can thrive also in the subalpine vegetation belt, on clear cuttings, burnt sites, rocky pastures and similar habitats, or form the mantle vegetation of subalpine forests, on sites of Fagus, Picea, Betula and Larix. The dominant species of this habitat is mainly Genista radiata, but also Genista holopetala and Genista hassertiana can be regarded as an element of illyric-tertiary flora and have a relict character. Shepherds favor grasslands and they often cut or burn these shrubby-habitats to provide more grazing area, but on the other hand abandonment of traditional land use leads to an increase of the surface occupied by this habitat.
Indicators of quality:
This vegetation can be threatened by (over)grazing, burning, extirpation of shrub for cultivation, global warming and urbanization. In the areas where it presents secondary vegetation it may be subject to succession towards forest.
The following characteristics may be considered as indicators of good quality:
dense stands with presence of diagnostic species

absence of tree species

moderate grazing

species richness


Characteristic species:
Flora: Asperula cynanchica, Bromus fibrosus, Calamagrostis varia, Carex laevus, C. sempervirens, Cerastium decalvans, Daphne blagayana, D. oleoides, Dorycnium germanicum, Erica carnea, Genista hassertiana, G. holopetala, G. radiata, Hypericum alpinum, Iberis sempervirens, Juniperus communis subsp. alpinus, Linum tauricum, Polygala chamaebuxus, Scabiosa columbaria, Sesleria latifolia, S. robusta, S. varia, Thymus longicaulis; on non-carbonate bedrock we can find also: Avenella flexuosa, Calamagrostis arundinacea, Calluna vulgaris, Festuca scabriculmis, Phyteuma scheuzeri, Vaccinium myrtillus.

Classification:
EUNIS:
F2.2 Evergreen alpine and subalpine heath and scrub
F2.3 Subalpine deciduous scrub        
EuroVegChecklist (alliance):
Daphno-Genistion radiatae N. Randelovic et Rexhepi 1980 
Annex 1:
4060 Alpine and boreal heaths
Emerald:
--
MAES-2:
Heathlands and scrub
IUCN ecosystems:
3.4 Temperate shrubland

Justification Outstanding Example of Biogeographical Region:
This habitat appears mainly in the Alpine region. It can be found in the mediterranean-montane vegetation belt but also in the southern outcrops of the Alps.

Map Description:
The map is rather incomplete but data availability is scarce. AOO and EOO are likely to be larger, therefore. Data sources: EVA, LIT, EXP.

Trends in Quantity:
On average a stable situation was detected in the EU28 situation in the past and likely also in the future (based on territorial data from Slovenia and Croatia). In the EU28+ an increasing trend of surface of this habitat was detected. In the past 50 years the increase was on average 23.5%, and predicted future trend is an increase of about 8.3%.

Trends in Quality:
The habitat is rather stable. No negative trend was detected within the EU28, but a small degradation of quality was analysed for the EU28 + (0.3 % of this habitat is 37% degraded). This habitat thrives mainly in areas or sites where few human activities occur.

Justification of Small Range/Regression:
The habitat range does not show an important decline in the past 50 years and it has a wide range, extending from the southern outcrops of the Alps to Thessaly in Greece.

Justification of Restricted Area:
In most sites the habitat has a very limited area, due to restricted suited conditions.

Pressures and Threats:
The pressures can be divided into three groups. Firstly there are human interventions, such as planting of trees, removal of shrubs (cutting or by fire), grazing, construction of ski resorts). Secondly succession and afforestation is a pressure in the subalpine belt. The third group consists of abiotic influence due to global warming, that may shift the vegetation upwards or to sites with cool aspects.

Conservation and Management:
No special treatment is needed. Grazing and removal of genistoid scrub should not be too intensive. On the other side, afforestation of these areas (especially under the timberline) should be precented. Finally, the occurrence of the habitat should be taken into account with planming of constructions in the mountains, like ski resorts.

Capacity to Recover its Typical Character and Functionality?:
If completely destroyed, the habitat needs a lot of time to recover due to extreme site conditions in mountains. If there are some shrub populations left nearby, one could roughly estimate that the habitat can recover within 20-30 years, with intervention (planting) even within 10-20 years.

Summary:
This genistoid scrub, dominated mainly by submediterranean Genista species, is found in the subalpine belt of mountains in southeastern Europe (centred on EU28+ Balkans) and the southern outcrops of the Alps. It forms dense stands mainly on carbonate and ultramaphic deposits, in rocky situations with rudimentary soils but a warm but humid microclimate. Although it can be a primary vegetation occuring in natural mosaics with alpine grasslands, it also spreads where forest has been cut or degraded or pasture abandoned. It is threatened by clearance and abandonment of grazing, by tourist developments and climate change. Thoughtful land management and planning are needed for conservation.

References:
Biondi E, Pinzi M, Gubelini (2004). Vegetatione e paesaggio vegetale del Massiccio del Monte Cucco (Appennino centrale - Dorsale Umbro-Marchigiana). Fitosociologia  41(2) supl.1: 3-81.
Franz WR, Leute GH (2010). Ein Neuvorkommen des Kugel-Ginsters (Genista radiata) im Gitschtal (Gailtaler Alpen) mit Hinweisen auf dessen Gesellschaftsanschluss in Kaernten un Julischen Alpen. Carinthia II 200: 383-392.
Lonati M (2006). Le communita a Genista radiata (L.) Scop. var. sericopetala Buccheger delle Alpi occidentali italiane. Fitosociologia 43(2): 97-110.
RanÄ‘eloviÄ‡ N, Rexhepi F & JovanoviÄ‡ V (1979). Biljne zajednice severoistoÄnog Kosova. In: Rauš, D. Drugi kongres ekologa Jugoslavije, Savez društava ekologa Jugoslavije 1, Zadar-Plitvice. pp. 957-995.

Criterion A Text:
A more or les stable trend in quantity was detected from the data provided by EU28 countries, but the data shjowed an increase of surface up to 23% in the EU28+. This increase was caused by abandonment of grazing leading to afforestation of pastures.

Criterion B Text:
The EOO is over the 50000 km2, and the number of locations is high. For the EU28 and EU28+ the AOO values meet the thresholds for criterion B2. However, exact figures are not known, because of lacking of precise distribution data, and it is likely that at least for EU28+ the value is over 50. Anyway, as there are no negative trends or threats overall assessment of criterion B leads to the conclusion Least Concern.

Criterion C/D Text:
The human impact in this habitat is low. There is a more or less stable quality in the EU28, and some slight negative trend in the EU28+.

Synthesis:
The habitat is assessed as Least Concerned (LC), as it is distributed in a rather large range and area and no reduction in quality and quantity has occurred in about the last 50 years.

Sub-habitats in Need of Examination:
The assessment is based mainly on Genista radiata dominated habitats. Less information is available and further research is needed on occurrences of Genista holopetala and Genista hassertiana (syn. Genista holopetala </em

Contributors:
Habitat description: A. ÄŒarni
Territorial data: E. Agrillo, F. Attorre,  A. ÄŒarni, L. Casella, R. Delarze, C. Giancola, D. Gigante, N. Juvan,  V. Matevski, F. Millaku, Ä. MilanoviÄ‡, G. Pezzi, D. Viciani, Å½. Škvorc.
Working Group Heathland & Scrub: M. Aronsson, F. Bioret, C. Bita-Nicolae, J. Capelo, A. ÄŒarni, P. Dimopoulos, J. Janssen, J. Loidi


Habitat Description:
The term 'dystrophic' is applied to a water body that is usually shallow, rich in humus giving its water a brown colour, with variable amounts of nutrients (though the availability of nutrients in most cases is low), and with the deeper water often depleted of oxygen. Most boreal lakes and ponds have humic substances in the water, but only polyhumic ones (with colour >90 Pt mg/L) are recognized as dystrophic here, the humic substances in the water being derived from mires, wetlands or paludified forests. Oligo- (< 30) and mesohumic (30 – 90 Pt mg/L) lakes and ponds are included in types based on their trophic state (habitats C1.1a, C1.1b and C1.2a, C1.2b).  In most dystrophic lakes and ponds the water is acid, (pH 3-6), but some have a higher pH, often caused by eutrophication. Bottom sediments consist of organogenic mud and debris, and the soft bottom can be some metres thick. Shores consist usually at least partially of peat, representing bog and fen communities, often quaking due to overgrowth from pond margins to the open water. Dystrophic pools with a similar appearance occur also in raised bog systems but as the origin of those pools is usually related to the development of mire complexes, they are included in the D habitats. Small dystrophic ponds (usually <10 hectares) and pools are often in contact with swamps and mires, therefore the water near the shores is often characterized by overgrowth of fen and bog vegetation. Floating-leaved plants are constant, elodeids and isoetids sparse. Potamogeton species are often missing, due to low nutrient status and pH. Freely floating and drifting aquatic mosses (Sphagnum spp., Warnstorfia spp., Drepanocladus spp., Fontinalis spp.) can be abundant. Utricularia minor and U. intermedia are characteristic species. The cover of helophytes and vascular shore plants varies, typical species being Carex lasiocarpa, C. rostrata, Phragmites australis, Equisetum fluviatile, Menyanthes trifoliata, Comarum palustre, Calla palustris etc. Moss cover, often dominated by Sphagnum spp., is well developed on shores.
In boreal regions there are many larger lakes with polyhumic water. Beside peaty shores they have mineral bottoms and shores, often of till or glacifluvial origin. Floristically these lakes are close to habitat C1.1b maintaining sparse stands of helophytes (Phragmites, Equisetum fluviatile, Schoenoplectus lacustris, Eleocharis palustris, Carex rostrata, C. lasiocarpa), floating-leaved macrophytes (Nymphaea alba, Nuphar lutea, N. pumila, Sparganium spp.), elodeids (Potamogeton perfoliatus, Myriophyllum alterniflorum) and isoetids (Isoëtes spp., Subularia aquatica, Eleocharis acicularis). Aquatic mosses are common. The vegetation of Lobelion dortmannae is typically occurring in this habitat type in oceanic Europe (e.g. Scandinavia and Ireland) but is absent in north-west European lowlands. Dystrophic water bodies are abundant in the boreal region with large mire areas, occurring typically on watersheds. They occur commonly in oceanic NW Europe as well but in continental Europe and southern Europe they are rare. Due to slow peat formation they are rare in northern boreal, arctic and alpine areas. Dystrophic lakes have deteriorated largely by forestry activities and drainage of peatlands for forestry, peat excavation etc., resulting in increase of humic substances, and in lowering of the water table. This has changed the bottom quality and depleted oxygen. Many lakes and ponds have also eutrophicated because of human habitation, construction activities and air-born nitrogen.
Indicators of good quality:
Water body has natural hydrology and water chemistry,
The pH should be < 6, colour >90 Pt mg/L,
Catchment area has undisturbed hydrology and natural land cover,
Typical structure of vegetation and co-existence of Utricularids, aquatic mosses, floating-leaved plants,
Intact shore vegetation,
Low anthropogenic influence, in terms of drainage, construction activities, forestry, water exploitation, and eutrophication,
Absence of invasive alien species.

Characteristic species:
Flora: Vascular plants: Sparganium minimum, S. angustifolium, S. emersum, Utricularia minor, U. intermedia, U. vulgaris, Juncus bulbosus, Myriophyllum alterniflorum, Potamogeton alpinus, P. perfoliatus, Isoëtes spp. Close to the shores are characterized by helophytes growing on organic muddy sediments such as Equisetum fluviatile, Comarum palustre, Calla palustris, Menyanthes trifoliata, Thelypteris palustris. Generalist macrophytes such as Nuphar spp., Nymphaea spp., Potamogeton natans, Phragmites australis, Typha angustifolia, T. latifolia, Schoenoplectus lacustris, Carex lasiocarpa, C. rostrata, and mire plants, such as Rhynchospora alba, Carex limosa, C. magellanica, Drosera longifolia, D. rotundifolia.
Mosses: Sphagnum cuspidatum, S. fallax, S. angustifolium, Calliergon spp., Warnstorfia spp. (W. procera, W. trichophylla), Fontinalis antipyretica, F. dalecarlica, Chiloscyphus polyanthos, Scapania spp.
Algae : Batrachospermum spp., Nitella flexilis, Chara spp. (occassional).
Fauna: Birds: Gavia stellata, Cygnus cygnus, Anas crecca. Insects: Chironomidae, Trichoptera, Odonata. Mammals: Castor fiber, Lutra lutra. Amphibians: Bufo spp, Triturus spp., Rana spp. Fish: Perca fluviatilis.

Classification:
EUNIS
C1.4 Permanent dystrophic lakes, ponds and pools
EuroVegChecklist alliances:
Sphagno-Utricularion T. Müller et Görs 1960
Subularion aquaticae Hadac 1971
Lobelion dortmannae Van den Berghen 1964, partly (Isoëto-Lobelion)
Sphagnion cuspidati Krajina 1934
Caricion lasiocarpae Van den Berghen in Lebrun et al. 1949
Annex 1:
3160 Natural dystrophic lakes and ponds
Emerald:
C1.4 Permanent dystrophic lakes, ponds and pools
MAES:
4.2.2 Freshwater ecosystem. Rivers and Lakes
IUCN:
5.5. Permanent Freshwater Lakes
5.7. Permanent Freshwater Marshes / Pools

Justification Outstanding Example of Biogeographical Region:
Dystrophic lakes, ponds and pools are characteristic of boreal and atlantic areas with humid, cool temperate climate with an active paludification process accumulating peat. Species assemblages in water ecosystems with high humus content are often highly specialized. The amphi-Atlantic element in the flora is representative of these conditions.

Map Description:
Map rather complete for EU28, but data gaps outside EU28 in Balkan and Switzerland. Data sources: Art17, EVA, GBIF.

Comment EU28:
might be 20-25 % higher due to gaps of data from countries

Comment EU28+:
data insufficient, Norway and Iceland are missing

Trends in Quantity:
Dystrophic waters are often situated on mire-rich lowland and watershed areas. Therefore their quantity has historically declined due to drainage of mires and land reclamation. This was earlier intensive in Central and Western Europe, particularly in the Netherlands, Germany, Austria, Czech Republic and Hungary. Negative trends have taken place in northern Europe as well, but their intensity was much lower. In the last 50 years and in the near future, the quantity of dystrophic waters seems to be more or less stable, showing some losses in the southern part of the European range. On the other hand, recent land use, as well as increased natural leaching of humic substances from the catchment areas due to climate change may increase amount of humus-rich waters (so called 'brownification of waters').

Trends in Quality:
The quality of the habitat has declined in Europe to a considerable extent during the last 50 years. The severity of degradation is 30% affecting 75% of its current area, on the basis of data from seven EU28 countries, including the major part of its extent. The figures are heavily determined by the large area of this habitat in Finland and, if Finnish data are excluded, the severity is somewhat higher. In Germany and Italy the quality has declined to considerable extent in the recent past. In some countries, the quality has been estimated to be stable or becoming better due to restoration and conservation measures.

% of Distribution of the Habitat Type within the EU 28:
Fresh-water bodies related to peatlands and areas under paludification have a wide distrubution in Eurasia and North America, particularly in boreal areas, but also in temperate and alpine areas, EU 28+ might constitute less than 10 % of the total area of these ecosystems globally.

Justification of Restricted Area:
The habitat has a large EOO but becomes more scattered in southern parts of its European range. These occurrences are in different situation as compared to the continuous main area in the northern Europe.

Pressures and Threats:
Dystrophic waters were earlier subjected to land reclamation and drainage, particularly in the Netherlands. At present, the main pressure affecting large areas is diffuse pollution caused by intensive land use, especially recent agricultural and forestry activities. Some pollution from human settlements and industrial sites occurs in many countries. In central Europe input from the air-borne pollutants, particularly nitrogen, is important. Beside pollution, changes in hydrology are another main pressure, caused by regulation of the water table or by water abstraction. Changes in hydrology cause low water levels, lack of flooding etc., in some cases drying of the habitat. Drainage of peatlands for forestry purposes and peat excavation increase humus load to waters, at least episodically, causing increased sedimentation, anoxia, and increased colour in the water. The nutrient input and changes in hydrological regimes is accelerating succession towards more eutrophic sites with denser littoral communities.

Conservation and Management:
Water protection measures decreasing nutrient and contaminant loading from the catchment areas are needed in many areas with intensive land use. That means in many cases changes in agricultural and forestry practices, resulting in lower loads of nutrients and humic substances. Another main approach is maintaining natural hydrology of the waters, meaning ecologically sound regulation regimes, maintaining natural flooding etc. Most representative sites should by protected (e.g. as Natura 2000 sites), and in some cases managed actively. Restoration activities are needed, including changes to natural hydrology, reduction of eutrophication, management of littoral communities, in extreme cases also removal of sediment.

Conservation Status:
Annex 1:
3160: ALP FV, ATL U2, BOR U1, CON U2, MAC U1, MED XX, PAN U2, STE XX

Capacity to Recover its Typical Character and Functionality?:
Many sites are able to recover after some ten of years. In sites with heavy eutrophication and/or changes in the hydrological regime, active intervention is needed. Natural recovery of the habitat can take place after intervention if pressures from land use in catchment areas are controlled. Restoration measures include changes in hydrology (often need to fill ditches etc.), management of littoral vegetation, removal of sediments etc.

Summary:
Dystrophic lakes, ponds and pools are characterized by dark brown water, usually shallow, rich in humic substances and generally of low nutrient content, with usually soft organic bottom sediments, the humus being derived from mires, wetlands and paludified forests. They occur particularly in the boreal region, often in watershed areas rich in mires but they are common also in Atlantic north-west Europe, though rare in more continental and in southern Europe. In alpine and arctic areas dystrophic waters are not common due to the slow paludification process. The plant communities are composed of many plants with a wide ecological amplitude, and often with an obvious contribution of mire species, notably Utricularia spp. and aquatic mosses, and there can be a contingent of shoreline or bog pool margin plants. Dystrophic water bodies have deteriorated largely due to land reclamation and drainage of peatlands for forestry, peat excavation and from eutrophication from settlements and air-born nitrogen. For recovery, these habitats require intervention, such as restoration of natural hydrology, filling of drainage ditches and removal of vegetation.

References:
Dierssen, K. 1996. Vegetation Nordeuropas. Verlag Eugen Ulmer, Stuttgart. 838 pp.
Leka, J. et al. 2008. Sisävedet ja rannat [Inland waters]. In Raunio, A., Schulman, A. & Kontula, T. (eds.), Suomen luontotyyppien uhanalaisuus [Assessment of threatened habitat types in Finland]. Osa 2. Luontotyyppien kuvaukset [Part 2. Habitat type descriptions]. Suomen Ympäristö / The Finnish Environment 8/2008: 89-142.
Påhlsson, l. (ed) 1994. Vegetationstyper i Norden. TemaNord 1994: 665. 626 pp.

Criterion A Text:
The reduction in quantity of the habitat was very pronounced in the Netherlands in the 19th and early 20th century. The land reclamation and drainage of dystrophic water bodies continued in many countries until the 1950s and 1960s. In the recent past (last 50 years) the quantity of the habitat has remained rather stable, and this seems to be the case also in the near future.

Criterion B Text:
Habitat type has a wide distribution and has many sites in various countries, therefore criterion B is not used in the European scale.

Criterion C/D Text:
Extent of degradation and relative severity of degradation were estimated using abiotic (physical and chemical parameters) and biotic parameters combined. Data derives often from the Art. 17 (Habitat Directive) and WPD reporting. Future trends might be stable or decreasing, partly because of the climate change. Data from extent of degradation was received from 13 countries and estimates for severity of degradation from 15 countries. Quantitative data combining extent and severity of degradation were available from 7 EU 28 countries, covering most of the area of the habitat.

Criterion E Text:
Quantitative analysis to evaluate risk of the habitat collapse has not been made.

Synthesis:
The quantity of the habitat declined severely in historical times, largely by large-scale land reclamation, suggesting category Vulnerable (VU) according to the criterion A3. However, the situation has since stabilized, therefore data from 50 last years have been used for the assessment. In the recent past the quality of the habitat has degraded clearly, severity of degradation being 30 %, affecting 75 % of current area. This is based on data from 7 countries with quantitative data from both extent of degraded area and severity of degradation. This data covers most of the habitat area. Criterion C/D1 qualifies the habitat to the category Near-Threatened (NT). Most area of the habitat in EU28+ occur in the EU28 area, therefore NT category may be used also for EU28+

Sub-habitats in Need of Examination:
Dystrophic waters cover a wide range of waters. Small ponds and pools, usually situating close to mires could be assessed separately from larger lakes. The latter have many features in general with C1.1a, C1.1b, sometimes also with C1.2b, and can be ev

Contributors:
Type description: H. Toivonen.
Territorial data: S. Armiraglio, G. Arts, S. Assini, S. Bell, C. Bita-Nicolae, J. Brophy, G. Buffa, J. Capelo, A. Carni, J-M. Couvruer, R. Delarze, L. Denys, D. Espírito-Santo, P. Finck, R. Hall, P. Ivanov, N. Juvan, G. Király, T. Kontula, H. Mäemets, A. Mikolajczak, J.A. Molina, D. Paelinckx, D. Paternoster, G. Pezzi, V. Rasomavicius, U. Raths, U. Riecken, J. Sibik, K. Sumberova, A. Ssymank, D. Viciani.
Working Group Freshwater Habitats: G. Arts, F. Landucci, J.A. Molina, B. Poulin, H. Toivonen


Habitat Type Name:
F7.4c Eastern Mediterranean mountain hedgehog-heath

Habitat Description:
This diverse habitat includes both the primary cushion heaths of the high, dry mountains of the East Mediterranean region with low, cushion-forming often spiny shrubs, and the secondary, zoogenic downslope extensions of these high-altitude formations. More specifically, it includes: (a) the shrubby formations of dry, usually calcareous rocky places with strongly eroded humus-carbonate soils, with large amounts of skeletal material and rock outcrops including the spiny hedgehog-heaths, the cushiony formations of dwarf suffrutescents and/or the bush-dominated facies of stripped grasslands, (b) the downslope extensions of the high altitude formations in zoogenic forest clearings of the mountains of Greece, of the Moesian zone and of the central Balkan peninsula which are dominated by the same species, or specifically montane or steppic taxa (often Genista-dominated), and (c) the high altitude hedgehog-heaths that are developed on relatively humus-rich rendziniform soils at or above treeline and dominated by large hemispherical tussocks of the tragacanths Astragalus rumelicus, and/or Astragalus parnassi. Varieties, distinguished by the dominant taxa, include the tragacanth dominated cushion heaths of the eastern Mediterranean; the Genista acanthoclada dominated formations; the summit communities of Mt. Troodos (in Cyprus) with Berberis cretica, Sorbus aria subsp. cretica (= S. graeca) that also include the restricted endemics Astragalus echinus, Alyssum troodii, Teucrium cyprium, Nepeta troodi, Satureja troodii, Onosma troodi and Scorzonera troodea; the endemic-rich hedgehog-heaths of calcareous mountains of Aegean islands and mount Athos (in Greece); as well as the hedgehog-heaths of high mountains of Crete with Astragalus creticus subsp. creticus, Astragalus angustifolius, Acantholimon androsaceum, Berberis cretica, Daphne oleoides, Prunus prostrata, Euphorbia acanthothamnos, Verbascum spinosum and Sideritis syriaca.
Indicators of good quality:
• High species richness and occurrence of endemic species
• Low shrub cover (chamaephytes, nano-phanerophytes) more than 30%
• Significant presence of perennial grass species
• Regular grazing
• No indication of strong erosion eg. gully formation
• Absence or low cover of ruderal/nitrophilous species (species of Stellarietea or of the Artemisietea)
• Long-term habitat stability: absence of progressive or retrogressive succesional trends
Characteristic species:
Acantholimon androsaceum, Achillea ageratifolia, Agropyron cristatum, Alyssum kionae, Alyssum troodii, Anthyllis aurea, Artemisia alba, Asperula cynanchica, Aster alpinus, Astragalus angustifolius, A. creticus subsp. creticus, A. echinus subsp. rumelicus, A. lacteus, A. parnassi, Berberis cretica, Bothriochloa ischaemum, Bromus riparius, B. scoparius, Centaurea chrysolepis, Cirsium hypopsilum (C. cylleneum), Convolvulus cochlearis, Daphne oleoides, Eryngium amethystinum, E. pusillum, Euphorbia acanthothamnos, Festuca dalmatica, F. stojanovii, F. thracica, Festucopsis sancta, Fumana procumbens, Genista acanthoclada, Globularia stygia, Hyacinthella leucophaea, Hypericum rumeliacum, Juniperus hemisphaerica, Linum flavum, Marrubium velutinum subsp. cylleneum, Minuartia stellata, Nepeta troodi, Onosma troodi, Paronychia kapela, Prunus prostrata, Rhodax canus, Rindera graeca, Satureja montana subsp. kitaibelii, S. troodii, Scorzonera troodea, Sesleria coerulans, Sideritis clandestina, S. scardica, S. syriaca, Sorbus aria subsp. cretica, Teucrium cyprium, T. montanum, Thymus boissieri, T. hirsutus, T. jankae, T. striatus, T. teucrioides, and Verbascum spinosum.

Classification:
EUNIS:
F7.4 Hedgehog-heaths
EuroVegChecklist:
Astragalo angustifolii-Seslerion coerulantis Quézel 1964
Eryngio multifidi-Bromion fibrosi Quézel 1964
Stipo pulcherrimae-Morinion persicae Quézel 1964
Astragalion cretici Bergmeier 2002
Verbascion spinosi Zaffran ex Bergmeier 2002
Colchico cretensis-Cirsion morinifolii Bergmeier 2002
Hyperico stenobotryos-Alyssion troodi S. Brullo et al. 2005
Asterion creticae Zaffran ex Bergmeier et al. 2011
Annex I:
4090 Endemic oro-Mediterranean heaths with gorse
Emerald:
F7 Spiny Mediterranean heaths (phrygana, hedgehog-heaths and related coastal cliff vegetation)
MAES 2:
Heathland and shrub
IUCN:
3.8 Mediterranean-type Shrubby Vegetation

Justification Outstanding Example of Biogeographical Region:
This unit includes the xeric zonal grasslands, dwarf-shrub and thorn-cushion communities of the mountains of the East Mediterranean territories (Greece, E-Aegean, NW and W Anatolia) as well as of Southern Bulgaria (near the borders to Greece). Together with the hedgehog heaths of the western and central Mediterranean region this is a typical habitat for the highest belts in Mediterranean mountains.

Map Description:
The map is complete or maybe a bit overestimated for the EU28, but the distribution in Macedonia and Albania is probably underestimated. Sources: EVA, Art17, GBIF.

Comment EU28:
Based on the existing data provided by the EU Member States (GR & BG). This number is partially representing the current actual total area.

Trends in Quantity:
The trend in quantity is more or less stable or slightly decreasing (<5%) based on the available territorial data.

Trends in Quality:
Both countries that have provided territorial data, report a stable situations with no trend in quality, although this is not documented by quantitative data. Overall in expert opinion, there is no negative trend in quality of the habitat throughout its distribution range.

Justification of Small Range/Regression:
The habitat is widespread at high altitudes of the Eastern Mediterranean and no deterioration of the structure and functions or of its ecological characteristics has been reported.

Justification of Restricted Area:
The habitat is widespread in the oro-mediterranean belt of the south Balkan and west Anatolian mountains.

Pressures and Threats:
The abandonment of summer pastoralism (which means lack of grazing) might be one of the most significant threats for the structure and functions of the habitat. The intensive grazing which once might have had significant effects on the floristic structure of the habitat and its sub-habitats, currently seems not the case in the mountain ranges of mainland and insular Greece (Crete, Evvoia and other large Aegean islands with high mountains, such as the island of Samos) because of the average decrease in the number of sheep and goats in the Greek mountains, although locally there can still be some evidence of heavily grazed areas. Another pressure and threat is the habitat fragmentation due to road construction up to the upper altitudinal mountain belts, which leads to a reduction of habitat connectivity or loss of specific habitat features.

Conservation and Management:
The grassland and dwarf-scrub/thorny-cushion vegetation communities of the Eastern Mediterranean mountain areas included in this habitat are used as summer pastures above the timberline since ancient times, traditionally with sheep and goats but recently also with cows and they have been indispensable for stock-breeding and grazing. The traditional character of the summer pastoralism which is still in practice should continue, avoiding heavy grazing through management measures for rational grazing intensity, and controlling the road and cistern constructions. Monitoring is necessary to study the combined effects of heavy grazing and all activities related to this.

Capacity to Recover its Typical Character and Functionality?:
Only the destruction of the habitat connectivity might affect dramatically habitat conservation. The time of recovery is related to/dependent on the disturbance or the destructive factor.

Summary:
This habitat includes both the primary cushion heaths of the high, dry mountains of the East Mediterranean region with low, cushion-forming, often spiny shrubs, and the secondary,  downslope extensions of these high-altitude communities developed through grazing. The dominant species vary in different regions and the flora includes endemics. The abandonment of summer pastoralism as well as heavy grazing are significant threats for the structure and function of the habitat, but there is also habitat fragmentation due to road construction up to higher altitudes. No conservation measures are necessary above the timberline if traditional practices continue.

References:
Bergmeier E (2002). The vegetation of the high mountains of Crete a revision and multivariate analysis. Phytocoenologia 32(2): 205-249
Georgiadis T, Dimopoulos P (1993). Etude de la vÄ—gÄ—tation supraforestiÄ—re du Mont Kyllini (PÄ—loponnÄ—se- GrÄ—ce). Botanica Helvetica 103 (2): 149-175.
Maroulis G, Georgiadis T (2005). The vegetation of supra–forest meadows and rock crevices of Mount Erimanthos (NW Peloponnisos, Greece). Fitosociologia 42 (1):33-56
Parolly G (2004). The High Mountain Vegetation of Turkey - a State of the Art Report, Including a First Annotated Conspectus of the Major Syntaxa. Turk J Bot 28: 39-63.

Criterion A Text:
A slight reduction in quantity has been reported from one of the countries (Bulgaria) that provided territorial data; less than 5% in the total extent of the habitat has been affected as has been reported.

Criterion B Text:
The habitat is widespread in the East Mediterranean mountain ranges (reaching to the southern limits of Bulgari) and Western Anatolia: large EOO and AOO (EOO > 50000 km2 and AOO > than 50 km2).

Criterion C/D Text:
Based on the countries that have provided data, reduction in quality is totally absent or affects a small area (0-5%) at low severity. The current trend regarding the biotic and abiotic quality of the habitat is stable to increasing.

Synthesis:
Although quantitative data on quality are lacking and also territorial data are not provided for all countries, the Red List criteria qualify for a Least Concern status. The extensive distribution of the habitat, with its varied plant communities throughout its range, in combination with the long-term interaction with traditional human activities (summer pasture-lands above the timberline), which has conserved the total species diversity and that of endemic/rare/endangered species, lead us with certainty to the same conclusion.

Sub-habitats in Need of Examination:
The altitudinally and ecologically differentiated alliances, and their corresponding vegetation communities (representing to the habitat sub-types) should be in the focus of further and systematic monitoring to detect species turnover related to the cl

Contributors:
Type description: P. Dimopoulos, F. Xystrakis
Territorial data: P. Dimopoulos, Ch. Gussev, V. Matevski
Working Group Heathland & Scrub: M. Aronsson, F. Bioret, C. Bita-Nicolae, J. Capelo, A. ÄŒarni, P. Dimopoulos, J. Janssen, J. Loidi


Habitat Type Name:
F3.1d Balkan-Anatolian submontane genistoid scrub

Habitat Description:
This habitat type comprises a complex of open shrub, herbaceous and chasmophytic plant communities dominated by the species complex of Genista rumelica/Genista lydia. It is an endemic type distributed to the southeastern part of the Balkan Peninsula (Southern Bulgaria and Northern Greece) and Asia Minor. The Genista rumelica communities are more widely distributed but restricted to the Balkans (endemic), whereas the communities of Genista lydia also occur in the western part of Anatolia. These communities are found mostly in lowland areas and lower parts of mountains on unstable sites (screes, steep slopes, rocky substrates). The genistoid scrubs grow mainly on sunny, dry, stony slopes with shallow soils of various bedrock (chalk, sandstones, volcanic stones). However, Genista rumelica prefers calcareous substrata. Because of its open structure the habitat is species rich with many elements from the Thero-Brachypodietea grasslands amongst which annual grasses (Brachypodium distachyon, Poa bulbosa, Psilurus incurvus, Bromus squarrosus), perennial grasses (Koeleria splendens, Chrysopogon gryllus) and many Balkan endemics (Achillea coarctata, Dianthus pinifolius, Silene frivaldszkyana). The communities can occupy secondary, degraded areas: screes and eroded places, replacing destroyed or degraded forest, mostly of different oak species, Oriental Hornbeam or Black Pine especially in Eastern Rodopi Mts. The habitat is characterized by open and complex structure consisting of patches with annual grasslands and low (0.5-1) genistoid scrublands where the tree individuals and high shrubs are either absent or in low numbers. The more open mosaics with other habitats exhibit the highest biodiversity (plant and animal species).
Indicators of quality:
· Relatively open scrublands in mosaic with other vegetation types;
· Presence of endemic shrub and herbaceous species;
· Absence or low number of trees and high (2-3 m) shrubs.
Characteristic species:
Flora, Vascular plants
Achillea coarctata, Alyssum murale, Brachypodium distachyon, Bromus squarrosus, Carpinus orientalis, Cephalaria laevigata, Chrysopogon gryllus, Cleistogenes serotina, Dianthus pinifolius, Dichanthium ischaemum, Fraxinus ornus, Genista lydia, G. rumelica, Jasmium fruticans, Juniperus oxycedrus, Koeleria spp., Melica ciliata, Minuartia setacea, Orlaya grandiflora, Poa bulbosa, Psilurus incurvus, Scabiosa ochroleuca, S. triniifolia, Sedum hispanicum, Silene frivaldszkyana, Stipa capillata, Teucrium chamaedrys, Thymus spp.

Classification:
EUNIS:
F3.29 Moesian broom fields
EuroVegChecklist:
Relationship unclear
Annex 1:
No relationship
Emerald:
No relationship
MAES-2:
Heathland and shrub
IUCN:
Temperate scrubland

Justification Outstanding Example of Biogeographical Region:
The habitat is distributed only in south-easternmost part of Europe and more specifically in Southern Bulgaria (continental) and Nothern Greece (Mediterranean region); this is considered more typical in Asia Minor of the Anatolian region.

Map Description:
The map gives a good picture of the range but within the range it may provide an underestimation due to lack of data. Data sources: EVA, NAT.

Trends in Quantity:
The habitat in Bulgaria has since long decreased its spatial extent (ploughing, quarries, etc); during the last 50 years the habitat has started increasing in extent (<10%) mainly due to the forest degradation caused by fires, overgrazing, etc. The trend in Greece is decline in spatial extent mostly due to the grazig abandoment and forest regeneration.

Trends in Quality:
No decline in habitat quality is observed in Bulgaria (stable status). The estimated trend in Greece is a slight decline in quality, mostly due to the abandoment of grazing and the subsequent forest regeneration.

% of Distribution of the Habitat Type within the EU 28:
About 40% of its current distribution lies within the EU 28. The habitat is also distributed in European Turkey and Western Anatolia.

Justification of Small Range/Regression:
The habitat is increasing during the last 50 years in Bulgaria. The trend in Greece is decline in extent but the lesser part of habitat''s range is in this country.

Justification of Restricted Area:
The habitat is increasing during the last 50 years in Bulgaria. The trends in Greece is decrease but the lesser part of habitat's range is in this country. The habitat has small natural range on the Balkans but bigger in the Anatolian Peninsula.</p

Pressures and Threats:
The main pressures/threats for the habitat are the following: mining and quarring activities, planting of artifitial forest plantations, overgrazing and abandonment of grazing followed by the ecological succession and invasion of shrub and forest species on the open places. However, the habitat has also a secondary distribution (especially in Bulgaria) on eroded terrains after forest degradation casuedd by fires, overgrazing, etc.

Conservation and Management:
The habitat has a narrow distribution and specific ecological features; its vegetation communities are floristically characterized by  regional endemic plant species and/or subspecies. However, this EUNIS habitat is not included to the Annex I of the Dir. 92/43/EEC and thus it has not been incorporated to any NATURA 2000 site. Its conservation through the legal identification of the habitat is necessary throughout its distribution range (either by inclusion of the habitat in the Annex I of the Dir. 92/43/EEC which is currently impossible or by the establishment of new Natura 2000 sites). Other conservation measures could focus a) on setting restriction rules for the construction of new quarries and mines, b) on proper management measures for forest planting, grazing activities, fires prevention, etc.

Conservation Status:
The habitat is not included in the Annex 1 of the Directive 92/43/EEC.

Capacity to Recover its Typical Character and Functionality?:
The habitat has the capacity to recover naturally or through intervention because it is typical to open places resulting from the natural geological and geomorphological processes, as well as from the grazing activities. The habitat can also expand its distribution on certain secondary eroded terrains.

Summary:
This scrub dominated by endemic genistoid shrubs is confined to Bulgaria and Greece in the Balkan Peninsula and, outside the EU28+, Asia Minor. It occurs in lowlands and foothills on unstable screes, steep slopes and outcrops of various rock types, mainly in dry, sunny situations with shallow soils, as a primary habitat or replacing destroyed or degraded forest.  It is threatened by mining and quarring, afforestation, overgrazing and abandonment, with succession to forest. Legal protection and limitation of disturbance are essential for conservation.

References:
Tzonev, R. & C. Gussev 2012. Mediterranean fields of Rumelian green weed (Genista rumelica) and Lydian green weed (Genista lydia). In: Biserkov, V., C. Gussev, V. Popov, G. Hibaum, V. Roussakova, I. Pandurski, Y. Uzunov, M. Dimitrov, R. Tzonev & Tsoneva, S. (eds.) Red Data Book of the Republic of Bulgaria. Vol. 3. Natural habitats.  BAS-MOEW, Sofia: 250-251.

Criterion A Text:
The extent of the habitat is increasing in Bulgaria but slightly decreasing in Greece. Totally, there is a slight decrease of 3%. Limited or lack of information for the historical and future trends of the habitat.

Criterion B Text:
The EOO is slightly above the threshold for criterion B, and the AOO (36 km2) below the threshold for criterion B. The habitat exists at relatively few locations, but it is estimated to be a more than 10 locations. In combination with small negative trends in quantity and quality, likely to continue, the habitat is assessed as Vulnerable under B2, and Near Threatened under B1.

Criterion C/D Text:
The extent of degradation is about 5%, while the severity of degradation is 40%. The general trend is slight decrease. The involved countries could not provide enough information on long historical or future trends in quality (CD2, CD3, C2, C3, and D2). The changes in quality are both abiotic (quarrying and mining) and biotic (grazing regime), so C/D1 has not been split into C1 and D1.

Synthesis:
The habitat type is assessed as Vulnerable (VU) in the EU28, due to a small distribution in combination with continuing (small) negative trends in quantity and quality (criterion B2). As far as known, the habitat does not occur outside the EU28 (within the Red List project region), and therefore the same categories apply for EU28+.

Contributors:
Habitat definition: R. Tzonev & I. Tsiripidis
Territorial data: Ch. Gussev, I. Tsiripidis
Working Group Heathland & Scrub: M. Aronsson, F. Bioret, C. Bita-Nicolae, J. Capelo, A. ÄŒarni, P. Dimopoulos, J. Janssen, J. Loidi


