Corynactis viridis and a mixed turf of crisiids, Bugula, Scrupocellaria, and Cellaria on moderately tide-swept exposed circalittoral rock

Photographer: Paul Brazier Copyright: Joint Nature Conservation Committee (JNCC)

Corynactis viridis and a mixed turf of crisiids, Bugula, Scrupocellaria, and Cellaria on moderately tide-swept exposed circalittoral rock

Photographer: Eleanor Murray Copyright: Joint Nature Conservation Committee (JNCC)

Map Key

Orange points: Core Records
Pale Blue points: Non-core, certain determination
Black points: Non-core, uncertain determination
Yellow areas: Predicted habitat extent

Biotope distribution data provided by the JNCC (mhc.jncc.gov.uk)

Researched by

Thomas Stamp, Kelsey Lloyd & Amy Watson

Refereed by

This information is not refereed

Researched by
Thomas Stamp, Kelsey Lloyd & Amy Watson

Refereed by
This information is not refereed

Summary

UK and Ireland classification

Standard	Classification	Description
EUNIS 2008	A4.132	Corynactis viridis and a mixed turf of crisiids, Bugula, Scrupocellaria, and Cellaria on moderately tide-swept exposed circalittoral rock
JNCC 2022	CR.HCR.XFa.CvirCri	Corynactis viridis and a mixed turf of crisiids, Bugula, Scrupocellaria, and Cellaria on moderately tide-swept exposed circalittoral rock
JNCC 2015	CR.HCR.XFa.CvirCri	Corynactis viridis and a mixed turf of crisiids, Bugula, Scrupocellaria, and Cellaria on moderately tide-swept exposed circalittoral rock
JNCC 2004	CR.HCR.XFa.CvirCri	Corynactis viridis and a mixed turf of crisiids, Bugula, Scrupocellaria, and Cellaria on moderately tide-swept exposed circalittoral rock
1997 Biotope	CR.ECR.EFa.CorCri	Corynactis viridis and a crisiid/Bugula/Cellaria turf on steep or vertical exposed circalittoral rock

EUNIS 2008 A4.132 - Corynactis viridis and a mixed turf of crisiids, Bugula, Scrupocellaria, and Cellaria on moderately tide-swept exposed circalittoral rock
JNCC 2015 CR.HCR.XFa.CvirCri - Corynactis viridis and a mixed turf of crisiids, Bugula, Scrupocellaria, and Cellaria on moderately tide-swept exposed circalittoral rock
JNCC 2004 CR.HCR.XFa.CvirCri - Corynactis viridis and a mixed turf of crisiids, Bugula, Scrupocellaria, and Cellaria on moderately tide-swept exposed circalittoral rock
1997 Biotope CR.ECR.EFa.CorCri - Corynactis viridis and a crisiid/Bugula/Cellaria turf on steep or vertical exposed circalittoral rock

Description

This biotope typically occurs on wave-exposed, vertical or steep, circalittoral bedrock or large boulders, usually subject to moderate or strong tidal streams. It is characterized by dense aggregations of the anemone Corynactis viridis and the cup coral Caryophyllia smithii intermixed with a short bryozoan turf of one or more Crisia spp., Scrupocellaria spp.,Bugula spp. and Cellaria spp. Occasionally, this turf obscures the underlying Corynactis virdis and Caryophyllia smithii. Cushion and encrusting sponges, particularly Pachymatisma johnstonia, Cliona celata, Esperiopsis fucorum and Dysidea fragilis, are present in moderate amounts at many sites. The axinellid sponges Stelligera spp. and Raspailia spp. are less frequently recorded. Clumps of large hydroids such as Nemertesia antennina and Nemertesia ramosa as well as the soft coral Alcyonium digitatum and the bryozoan Alcyonidium diaphanum may be found covering the hard substratum. The anemones Actinothoe sphyrodeta and Cylista elegans are typically present in low numbers, while the hard `coral' Pentapora foliacea is also occasionally observed. The most frequently recorded echinoderms are Marthasterias glacialis and Asterias rubens, although other species such as Echinus esculentus may also be seen. The rocky substratum may have a patchy covering of encrusting red seaweeds/algae. The crabs Necora puber and Cancer pagurus may be seen in crevices or under overhangs. This biotope is regularly recorded around south west England and Wales, often on vertical rock faces. (Information from Connor et al., 2004).

Depth range

10-20 m, 20-30 m

Additional information

Listed By

Annex 1

Sensitivity reviewHow is sensitivity assessed?

Sensitivity characteristics of the habitat and relevant characteristic species

CR.HCR.XFa.CvirCri occurs on wave-exposed, vertical or steep, circalittoral bedrock or large boulders, usually subject to moderate or strong tidal streams. It is characterized by dense aggregations of the anemone Corynactis viridis and the cup coral Caryophyllia smithii intermixed with a short bryozoan turf of one or more Crisia spp., Scrupocellaria spp., Bugula spp. and Cellaria spp. Cushion and encrusting sponges, particularly Pachymatisma johnstonia, Cliona celata, Esperiopsis fucorum and Dysidea fragilis, are present in moderate amounts at many sites (Connor et al., 2004). For this sensitivity assessment, Corynactis viridis, Caryophyllia smithii, and the bryozoan turf species; Crisia spp., Scrupocellaria spp., Bugula spp. and Cellaria spp. are the primary foci of research. Cushion and encrusting sponges, particularly Pachymatisma johnstonia, Cliona celata, Esperiopsis fucorum and Dysidea fragilis as well as Alcyonium digitatum are also mentioned throughout, however, the sensitivity assessments within this review are largely based on the Corynactis viridis, Caryophyllia smithii and bryozoans within this biotope.

Resilience and recovery rates of habitat

Corynactis viridis is a small anemone, with a base up to 10 mm in diameter and up to 15 mm in height (Ager, 2007), which grows on sublittoral rock walls and shaded parts of ship wrecks (Wood, 2007). Corynactis viridis is distributed from the North Shetland, UK (Ager, 2007) to the Iberian peninsula (Ramos, 2010) and Greece (Koukouras, 2010). Little is known on sexual reproduction or recruitment within this species. Hiscock et al. (2010) observed Corynactis viridis recruited onto the wreck of the Scylla within a year of the vessel sinking (see below). Corynactis viridis can reproduce via a-sexual budding, which can cause dense aggregations of uni-coloured clones.

Caryophyllia smithii is a small (max 3 cm across) solitary coral common within tide swept sites of the UK (Wood, 2005), distributed from Greece (Koukouras, 2010) to the Shetland Islands and southern Norway (NBN, 2015). It was suggested by Fowler & Laffoley (1993) that Caryophyllia smithii was a slow growing species (0.5-1 mm in horizontal dimension of the corallum per year), which in turn suggests that inter-specific spatial competition with colonial faunal or algae species are important factors in determining local abundance of Caryophyllia smithii (Bell & Turner, 2000). Caryophyllia smithii reproduces sexually; sessile polyps discharge gametes typically from January-April, gamete release is most likely triggered by seasonal temperature increases, gametes are fertilized in the water column and develop into a swimming planula, which then settles onto the suitable substrata. The pelagic stage of the larvae may last up to 10 weeks, which provides this species with a good dispersal capability (Tranter et al., 1982).

Crisia spp., Scrupocellaria spp., Bugula spp. and Cellaria spp. are erect active suspension feeding bryozoans which grow erect pinnate colonies to a maximum of 3-6 cm height from the seabed. Within the bryozoan genera described above there are many species distributed across the British Isles, however within the biotope description no particular species is mentioned, and therefore the evidence presented within this review covers all species within the mentioned genera. No evidence was found that Crisia spp., Scrupocellaria spp. records from the North East Atlantic occurred further north than Shetland, UK. Bugula spp. have however been recorded up to Trondheim, Norway (Christie et al., 2003). Crisia spp. have a wide distribution within the Atlantic, for example; Crisia denticulata, Crisia elongata, Crisia ramosa are recorded to as far south as the Gulf of Mexico. Scrupocellaria spp. southern limit in the North East Atlantic is the Iberian peninsula (Ramos, 2010). Bugula neritina is recorded from the Arabian sea (Molnar et al., 2008) Bugulina turbinata (syn. Bugula turbinata) and Crisularia plumosa (syn. Bugula plumosa) is recorded to the iberian peninsula (Ramos, 2010).

Bugula spp. and other bryozoan species exhibit multiple generations per year (see below), that involve good local recruitment, rapid growth and reproduction. Bryozoans are often opportunistic, fouling species that colonize and occupy space rapidly. For example, hydroids would probably colonize with 1-3 months and return to their original cover rapidly; while Bugula species have been reported to colonize new habitats within 6 -12 months. However, Bugula has been noted to be absent form available habitat even when large populations are nearby (Castric-Frey, 1974; Keough & Chernoff, 1987), suggesting that recruitment may be more sporadic (Tyler-Walters, 2002).

Where the population is reduced in extent or abundance but individuals remain, local recruitment, augmented by dormant resistant stages and asexual reproduction, is likely to result in rapid recovery of the dominant bryozoan species, probably within 12 months. The brooded, lecithotrophic coronate larvae of many bryozoans (e.g. Flustra foliacea, Securiflustra securifrons, and Bugula species), have a short pelagic lifetime of several hours to about 12 hours (Ryland, 1976). Recruitment is dependent on the supply of suitable, stable, hard substrata (Eggleston, 1972b; Ryland, 1976; Dyrynda, 1994). However, even in the presence of available substratum Ryland (1976) noted that significant recruitment in bryozoans only occurred in the proximity of breeding colonies. For example, Hatcher (1998) reported colonization of slabs, suspended 1 m above the sediment, by Bugulina fulva (syn. Bugula fulva) within 363 days while Castric-Fey (1974) noted that Bugulina turbinata, Crisularia plumosa and Bugulina calathus (syn. Bugula calathus) did not recruit to settlement plates after ca two years in the subtidal even though present on the surrounding bedrock. Similarly, Keough & Chernoff (1987) noted that Bugula neritina was absent from areas of seagrass bed in Florida even though substantial populations were present <100m away.

Alcyonium digitatum is a colonial species of soft coral with a wide distribution in the North Atlantic, recorded from Portugal (41°N) to Northern Norway (70°N) as well as on the east coast of North America (Hartnoll, 1975; Budd, 2008). Colonies consist of stout “finger like” projections (Hartnoll, 1975) which can reach up to 20 cm tall (Budd, 2008) and can dominate circalittoral rock habitats (as in CR.HCR.FaT.CTub.Adig; Connor et al., 2004). Alcyonium digitatum colonies are likely to have a lifespan which exceeds 20 years as colonies have been followed for 28 years in marked plots (Lundälv, pers. comm., in Hartnoll, 1998). Those colonies which are 10-15 cm in height have been aged at between 5 and 10 years old (Hartnoll, unpublished). Most colonies are unisexual, with the majority of individuals being female. Sexual maturity is predicted to occur, at it’s earliest, when the colony reaches it’s second year of growth, however the majority of colonies are not predicted to reach maturity until their third year (Hartnoll, 1975). As documented within Whomersley & Picken (2003) and Hiscock et al. (2010) (see below), Alcyonium digitatum can recruit within 1-2 years, however may require a further 5 years to become fully established.

Cliona celata is considered a hardy sponge, tolerant of environmental stressors such as high nutrient loads, low salinity, and large temperature variation (Duckworth & Peters, 2013). Cliona celata is a physically distinctive species of sponge that can bore into soft rock (e.g. limestone) or in hard rock areas has a massive form (Wood, 2007). The boring form is recognizable as yellow papillae sticking out of limestone (calcareous rock, mollusc shells). The massive form has raised, rounded ridges up to 40 cm across. Large oscules with raised rims are found along the tops of the ridges. It often forms a thick plate-like structure standing on its edge with large specimens growing up to 1 m across and 50 cm high (Snowden, 2007). According to the World Porifera database, Cliona celata has a relatively cosmopolitan distribution from north of Shetland to the cape of good hope, South Africa, as well as being recorded throughout the Mediterranean (Van Soest, 2016). No specific information for Cliona celata longevity was found, however, in general, sponges have a relatively long lifespan, e.g. Ayling (1983) estimated sponge patches in New Zealand were over 70 years old. Piscitelli et al. (2011) observed an annual peak in reproductive activity in April-May from individuals in the Mediterranean, and suggested this was a result of a sharp seasonal increase in water temperature. However, Carver et al. (2010) suggested Cliona celata specimens from New Brunswick, Canada spawned from June-July. Recruitment can occur via larval settlement as well as through transfer or contact, i.e. sponge colonies can spread to new or virgin substrata if they come in contact with existing colonies (Duckworth & Peterson, 2013). Warburton (1966) documented the spawning of Cliona celata under laboratory conditions, and reported the production of motile larvae that settled after 2 days (Carver et al., 2010). Information concerning colonization rates are scare however, tropical clionid sponges (the same taxonomic family as Cliona celata) can colonize dead coral within “a few weeks” and live coral within 2-3 months (Schönberg & Wilkinson, 2001). Furthermore, the short larval period (2 days) plus observation from Carver et al. (2010) indicate Cliona celata can colonize virgin surfaces within a year. Cliona celata is a pest species in scallop aquaculture. Carver et al. (2010) demonstrated that contact between shells colonized with Cliona celata and those that were not colonized results in rapid spread in Cliona celata throughout scallop farms. Once settled, Cliona celata colonies have a rapid growth rate of up to 15 cm²/yr (Carver et al., 2010).

Whomersley & Picken (2003) documented epifauna colonization of offshore oil platforms in the North Sea from 1989-2000. On all platforms Mytilus edulis dominated the near surface community. For the first 3 years, hydroids and tubeworms dominated the community below the mussel band. However the hydroid community were later out-competed by other more climax communities. Recruitment of Alcyonium digitatum and Metridium senile began at 2-5 years (dependent on the oil rig). The community structure and zonation differed between the four rigs, however, after four years Metrdium senile had become the dominant organism below the mussel zone to approximately 60-80 m Below Sea Level (BSL). Zonation differed between oil rigs, however, from approximately 60-90 m BSL Alcyonium digitatum was the dominant organism.

The Scylla was intentionally sunk on the 27^th March 2004 in Whitsand Bay, Cornwall to act as an artificial reef. Hiscock et al. (2010) recorded the succession of the biological community on the wreck for five years following the sinking of the ship. Initially the wreck was colonized by opportunistic species /taxa; filamentous algae, hydroids, serpulid worms and barnacles. Tubularia sp. were early colonizers, appearing within a couple of months after the vessel was sunk. Metridium senile appeared late in the summer of the first year, but didn’t become visually dominant until 2007 (three years after the vessel was sunk). Sagartia elegens was recorded within the summer of 2005, and by the end of 2006 was well established. Corynactis viridis was first recorded in the summer of the first year and quickly formed colonies via asexual reproduction. Urticina felina was first recorded at the end of August 2006 (2 years after the vessel was sunk), and by summer 2008 had increased in abundance. Alcyonium digitatum was first recorded in early summer 2005, a year after the vessel was sunk. Within one year of growth colonies had grown to nearly full size, however, did not become a visually dominant component of the community until 2009 (five years after the vessel had been sunk). The authors noted that erect branching Bryozoa (such as Securiflustra securifrons) are not a common part of rocky reef communities to the west of Plymouth and had not colonized to any great extent on Scylla by the end of the study, although several species were recorded, which included Chartella papyracea in 28/08/2006 (two years after the vessel was sunk). Caryophyllia smithii was noted to colinize the wreck a year after the vessel was sunk.

Jensen et al. (1994) reported the colonization of an artificial reef in Poole Bay, England. They noted that erect bryozoans, including Bugulina plumosa, began to appear within six months, reaching a peak in the following summer, 12 months after the reef was constructed. Similarly, ascidians colonized within a few months e.g. Aplidium spp. Sponges were slow to establish with only a few species present within 6-12 months but beginning to increase in number after two years, while anemones were very slow to colonize with only isolated specimens present after 2 years (Jensen et al., 1994.). In addition, Hatcher (1998) reported a diverse mobile epifauna after a years’ deployment of her settlement panels.

Resilience assessment. Overall, bryozoans are opportunistic, grow and colonize space rapidly and will probably develop a faunal turf within 1-2 years. Similarly, as reported by Hiscock et al. (2010), both Corynactis viridis and Caryophyllia smithii can colonize virgin surfaces within a year but the community may take another year to become established. Therefore, resilience has been assessed as ‘High’.

Hydrological Pressures

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	Resistance	Resilience	Sensitivity
Temperature increase (local) [Show more] Temperature increase (local) Benchmark. A 5°C increase in temperature for one month, or 2°C for one year. Further detail Evidence Corynactis viridis is distributed from the North Shetland, UK (Ager, 2007) to the Iberian peninsula (Ramos, 2010) and Greece (Koukouras, 2010). Mature examples of Caryophyllia smithii are recorded in Greece (Koukouras, 2010), and are therefore unlikely to be physically affected at the benchmark. However, Tranter et al. (1982) suggested Caryophyllia smithii reproduction was cued by seasonal increases in seawater temperature. Therefore, unseasonal increases in temperature may disrupt natural reproductive processes and negatively influence recruitment patterns. Some Crisia and Bugula species have been recorded from the gulf of Mexico and Arabian sea (respectively), where sea surface temperature far exceeds that experienced within the British Isles. However, Scrupocellaria and a number of Bugula spp. have a southern limit at the Iberian Peninsula (Ramos, 2010) (in their North East Atlantic distribution), where average annual temperature is approximately 2-4°C higher (Temp taken from San Sebastian, Beszczynska-Möller & Dye, 2013) than in the south west of the UK (temp taken from Plymouth, Beszczynska-Möller & Dye, 2013). Menon (1972) demonstrated that encrusting bryozoan species (Membranipora membranacea, Electra pilosa and Conopeum reticulum) were capable of acclimating to acute temperature increases of up to 5°C before significant mortality occurred. No similar information was available for the specific bryozoan genera assessed within this review, however, all three species can be found in the sub littoral and therefore could indicate heat acclimation response within Bryozoa. CR.HCR.XFa.CvirCri is distributed from the Cornwall, west coast of Wales and potentially North West Ireland. Sea surface temperature across this distribution ranges 8-16°C in summer and 6-13°C in winter (Beszczynska-Möller & Dye, 2013). Sensitivity assessment. All the characterizing species within CR.HCR.XFa.CvirCri are recorded from the Iberian peninsula and are therefore unlikely to be affected by a 2°C for one year. Bryozoa have been shown to acclimate to 5°C temperature increases before significant mortality occurs. Acute temperature increases may, however, negatively affect anthozoan reproduction and hence recruitment. Resistance has been assessed as ‘Medium’, resilience has been assessed as ‘High’. Sensitivity has been assessed as ‘Low’.	Low Low NR NR Help	High High High High Help	Low Low Low Low Help
Temperature decrease (local) [Show more] Temperature decrease (local) Benchmark. A 5°C decrease in temperature for one month, or 2°C for one year. Further detail Evidence Corynactis viridis is distributed from the North Shetland, UK (Ager, 2007) to the Iberian peninsula (Ramos, 2010) and Greece (Koukouras, 2010). Caryophyllia smithii has a northern range limit in the Shetland isles and southern Norway (NBN, 2015). The bryozoan taxa within CR.HCR.XFa.CvirCri have their northern range limit (North East Atlantic) within north Scotland and/or mid-Norway. CR.HCR.XFa.CvirCri is distributed from Cornwall, the west coast of Wales and potentially north-west Ireland. Sea surface temperature across this distribution ranges 8-16°C in summer and 6-13°C in winter (Beszczynska-Möller & Dye, 2013). Sensitivity assessment. All the characterizing species within CR.HCR.XFa.CvirCri may be limited by cold temperatures within the UK, and may explain the south westerly distribution of this CR.HCR.XFa.CvirCri. Resistance has been assessed as ‘Low’, resilience as ‘High’. Sensitivity has been assessed as ‘Low’.	Low Low NR NR Help	High High High High Help	Low Low Low Low Help
Salinity increase (local) [Show more] Salinity increase (local) Benchmark. A increase in one MNCR salinity category above the usual range of the biotope or habitat. Further detail Evidence Corynactis viridis and Caryophyllia smithii are recorded in the Mediterranean. Some Crisia and Bugula species have been recorded from the gulf of Mexico and Arabian sea (respectively). Therefore, some of the characterizing species are likely to tolerate 39-40 psu. However, a significant increase in salinity beyond this range may cause declines in abundance. Sensitivity assessment. Resistance has been assessed as ‘Low’, resilience as ‘High’. Sensitivity has been assessed as ‘Low’.	Low Low NR NR Help	High High High High Help	Low Low Low Low Help
Salinity decrease (local) [Show more] Salinity decrease (local) Benchmark. A decrease in one MNCR salinity category above the usual range of the biotope or habitat. Further detail Evidence In general, there is a scarcity of Corynactis viridis or Caryophyllia smithii records as important characterizing species from reduced salinity biotopes (Connor et al., 2004) indicating that these species require full salinity (30-40‰) to dominate the substrata. Ryland (1970) stated that, with a few exceptions, the Gymnolaemata bryozoans (the taxonomic class that Bugula spp. are a part of) were fairly stenohaline and restricted to full salinity (ca 35 psu) and noted that reduced salinities result in an impoverished bryozoan fauna. Soule & Soule (1979) suggested that some species of Bugula may be considered euryhaline, e.g. Bugula neritina and Bugulina californica occur in harbours subject to large freshwater runoff. Lynch (cited in Hyman, 1959) reported that reduced salinity delayed metamorphosis in larvae of Bugula neritina but not in Bugulina flabellata or Crisularia turrita (syn. Bugula turrita). Bugulina turbinata populations in the intertidal are likely to be exposed to freshwater runoff and rainfall. Sensitivity review. CR.HCR.XFa.CvirCri is restricted to full marine conditions (30-40 ‰) (Connor et al., 2004). The lack of records within “Reduced” salinity (18-30‰) suggests the community would not persist/be recognisable if salinity was reduced. Resistance has been assessed as ‘Low’, resilience as ‘High’ and sensitivity as ‘Low’.	Low Low NR NR Help	High High High High Help	Low Low Low Low Help
Water flow (tidal current) changes (local) [Show more] Water flow (tidal current) changes (local) Benchmark. A change in peak mean spring bed flow velocity of between 0.1 m/s to 0.2 m/s for more than one year. Further detail Evidence The biological community within CR.HCR.XFa.CvirCri is dominated by suspension feeders that rely on water currents to supply food. These taxa are therefore likely to thrive in conditions of vigorous water flow. Corynactis viridis or Caryophyllia smithii, in particular, are described as favouring sites with high water flow or surge currents (Bell & Turner, 2000; Wood, 2005). Water flow has been shown to be important for the development of bryozoan communities and the provision of suitable hard substrata for colonization (Eggleston, 1972b; Ryland, 1976). In addition, areas subject to the high mass transport of water such as the Menai Strait, Wales, or tidal rapids generally support large numbers of bryozoan species. Okamura (1984) reported that an increase in water flow from slow flow (0.01-0.02 m/s) to fast flow (0.1-0.12 m/s) reduced feeding efficiency in small colonies but not in large colonies of Bugulina stolonifera. Bugulina turbinata has also been recorded from strong to weak tidal streams (0.5-3 m/sec) (Tyler-Walters, 2005c). Sensitivity assessment. CR.HCR.XFa.CvirCri is recorded from moderately strong-strong tidal streams (0.5-3m/sec) (Connor et al., 2004), furthermore, all the characterizing species are reliant on high water flow for food supply. A change in tidal velocity of 0.1-0.2 m/s is not likely to have a significant effect on the biotope. Resistance has been assessed as ‘High’, resilience has been assessed as ‘High’. Sensitivity has been assessed as ‘Not sensitive’.	High Medium High High Help	High High High High Help	Not sensitive Medium High High Help
Emergence regime changes [Show more] Emergence regime changes Benchmark. 1) A change in the time covered or not covered by the sea for a period of ≥1 year or 2) an increase in relative sea level or decrease in high water level for ≥1 year. Further detail Evidence Changes in emergence are not relevant to CR.HCR.XFa.CvirCri which is restricted to fully subtidal/circalittoral conditions. The pressure benchmark is relevant only to littoral and shallow sublittoral fringe biotopes.	Not relevant (NR) NR NR NR Help	Not relevant (NR) NR NR NR Help	Not relevant (NR) NR NR NR Help
Wave exposure changes (local) [Show more] Wave exposure changes (local) Benchmark. A change in near shore significant wave height of >3% but <5% for more than one year. Further detail Evidence CR.HCR.XFa.CvirCri is recorded from very exposed – moderately wave exposed sites (Connor et al., 2004). Caryophyllia smithi, Corynactis viridis and bryozoans are suspension feeders relying on water currents to supply food. These taxa, therefore, thrive in conditions of vigorous water flow. Caryophyllia smithi and Corynactis viridis are small anemones (see resilience section) who are unlikely to exceed >3 cm height from the seabed. The small size of these anemones is, therefore, likely to reduce friction caused by the surrounding water flow, and reduce the risk of these species from being removed from rock surfaces. Bugula spp. produce flexible erect tufts, which are likely to move with the oscillatory flow created by wave action. Bugula, Bugulina and Crisiidae have all been recorded from very wave exposed biotopes (Connor et al., 2004; Tyler-Walters, 2005c). Sensitivity assessment. Wave action is a fundamental environmental variable controlling the biological community of sub-littoral biotopes. A large and significant change in wave height may fundamentally alter the character of CR.HCR.XFa.CvirCri. However, a change in near shore significant wave height of 3-5% is not likely to have a significant effect on the biological community. Resistance has been assessed as ‘High’, resilience has been assessed as ‘High’. Sensitivity has been assessed as ‘Not sensitive’.	High Low NR NR Help	High High High High Help	Not sensitive Low Low Low Help

Chemical Pressures

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	Resistance	Resilience	Sensitivity
Transition elements & organo-metal contamination [Show more] Transition elements & organo-metal contamination Benchmark. Exposure of marine species or habitat to one or more relevant contaminants via uncontrolled releases or incidental spills. Further detail Evidence This pressure is Not assessed but evidence is presented where available. No information was found relating to the sensitivity of Caryophyllia smithii or Corynactis viridis to heavy metal contamination. Bryozoans are common members of the fouling community and amongst those organisms most resistant to antifouling measures, such as copper-containing anti-fouling paints (Soule & Soule, 1979; Holt et al., 1995). Most of the information found concerning the toxicity of metals to this genus concerned Bugula neritina. Lee & Trot (1973) reported that Bugula neritina colonized wooden panels treated with copper based antifouling paints and dominated the succession after 5-7 weeks. Bugula neritina was reported to survive but not grow exposed to ionic Cu concentrations of 0.2-0.3 ppm, while larvae died above 0.3ppm (Soule & Soule, 1979). Similarly, Ryland (1967) reported that Bugula neritina died where the surface leaching rate of Cu exceeded 10 µg Cu/cm²/day, while ancestrulae may recover from prolonged Cu exposure if transferred to clean seawater. Ryland (1967) also noted that Bugula neritina was less intolerant of Hg than Cu. Copper ion concentrations greater than 2.5 mg CuCl₂/l stimulated a change from positive to negative phototactic response in Bugulina simplex (Ryland, 1967).	Not Assessed (NA) NR NR NR Help	Not assessed (NA) NR NR NR Help	Not assessed (NA) NR NR NR Help
Hydrocarbon & PAH contamination [Show more] Hydrocarbon & PAH contamination Benchmark. Exposure of marine species or habitat to one or more relevant contaminants via uncontrolled releases or incidental spills. Further detail Evidence This pressure is Not assessed but evidence is presented where available. CR.HCR.XFa.CvirCri is a sub-tidal biotope (Connor et al., 2004). Oil pollution is mainly a surface phenomenon its impact upon circalittoral turf communities is likely to be limited. However, as in the case of the Prestige oil spill off the coast of France, high swell and winds can cause oil pollutants to mix with the seawater and potentially negatively affect sublittoral habitats (Castège et al., 2014). Smith (1968) reported dead colonies of Alcyonium digitatum at a depth of 16 m in the locality of Sennen Cove, Cornwall which was likely a result of toxic detergents sprayed along the shoreline to disperse oil from the Torrey Canyon tanker spill (Budd, 2008). No information was found relating to the sensitivity of Caryophyllia smithii or Corynactis viridis to hydrocarbon contamination. Soule & Soule (1979) reported that Bugula neritina was lost from breakwater rocks in the vicinity of the December 1976 Bunker C oil spill in Los Angeles Harbour, and had not recovered within a year. However, it had returned to a nearby area within 5 months even though the area was still affected by sheens of oil. Similarly, Mohammad (1974) reported that Bugula spp. and Membranipora spp. were excluded from settlement panels near a Kuwait oil terminal subject to minor but frequent oil spills.	Not Assessed (NA) NR NR NR Help	Not assessed (NA) NR NR NR Help	Not assessed (NA) NR NR NR Help
Synthetic compound contamination [Show more] Synthetic compound contamination Benchmark. Exposure of marine species or habitat to one or more relevant contaminants via uncontrolled releases or incidental spills. Further detail Evidence This pressure is Not assessed but evidence is presented where available. No information was found relating to the sensitivity of Caryophyllia smithii or Corynactis viridis to synthetic compound contamination. Bryozoans are common members of the fouling community and amongst those organisms most resistant to antifouling measures, such as copper-containing anti-fouling paints (Soule & Soule, 1979; Holt et al., 1995). Bryan & Gibbs (1991) reported that there was little evidence regarding TBT toxicity in Bryozoa with the exception of the encrusting Schizoporella errata, which suffered 50% mortality when exposed for 63 days to 100 ng/l TBT. Rees et al. (2001) reported that the abundance of epifauna (including bryozoans) had increased in the Crouch estuary in the five years since TBT was banned from use on small vessels. This last report suggests that bryozoans may be at least inhibited by the presence of TBT. Moran & Grant (1993) reported that settlement of marine fouling species, including Bugula neritina, was significantly reduced in Port Kembla Harbour, Australia, exposed to high levels of cyanide, ammonia and phenolics. Note, however, that Bugula neritina is a warm temperate species probably only remotely related to the NE Atlantic species (P. Hayward, pers. comm.). Hoare & Hiscock (1974) suggested that polyzoa were amongst the most sensitive species to acidified halogenated effluents in Amlwch Bay, Anglesey and noted that Bugulina flabellata did not occur within the bay.	Not Assessed (NA) NR NR NR Help	Not assessed (NA) NR NR NR Help	Not assessed (NA) NR NR NR Help
Radionuclide contamination [Show more] Radionuclide contamination Benchmark. An increase in 10µGy/h above background levels. Further detail Evidence 'No evidence' was found	No evidence (NEv) NR NR NR Help	Not relevant (NR) NR NR NR Help	No evidence (NEv) NR NR NR Help
Introduction of other substances [Show more] Introduction of other substances Benchmark. Exposure of marine species or habitat to one or more relevant contaminants via uncontrolled releases or incidental spills. Further detail Evidence This pressure is Not assessed	Not Assessed (NA) NR NR NR Help	Not assessed (NA) NR NR NR Help	Not assessed (NA) NR NR NR Help
De-oxygenation [Show more] De-oxygenation Benchmark. Exposure to dissolved oxygen concentration of less than or equal to 2 mg/l for one week (a change from WFD poor status to bad status). Further detail Evidence In general, respiration in most marine invertebrates do not appear to be significantly affected until extremely low concentrations are reached. For many benthic invertebrates, this concentration is about 2 ml/l, or even less (Herreid, 1980; Rosenberg et al., 1991; Diaz & Rosenberg, 1995). No information was found relating to the sensitivity of Corynactis viridis to de-oxygenation. There is anecdotal evidence to suggest that Alcyonium digitatum, Caryophyllia smithii hypoxic events. Alcyonium digitatum mainly inhabits environments in which the oxygen concentration usually exceeds 5 ml/l and respiration is aerobic (Budd, 2008). In August 1978 a dense bloom of a dinoflagellate, Gyrodinium aureolum occurred surrounding Geer reef in Penzance Bay, Cornwall and persisted until September that year. Observations by local divers indicated a decrease in underwater visibility (<1 m) from below 8 m Below Sea Level. It was also noted that many of the faunal species appeared to be affected, e.g. no live Echinus esculentus were observed whereas on surveys prior to August were abundant. Alcyonium sp. and Bryozoans were also in an impoverished state. Caryophyllia smithii were also in a contracted state, apparently dead, and with Echinus esculentus were the worst affected species during the bloom. During follow-up surveys conducted in early September Alcyonium sp. were noted to be much healthier and feeding. It was suggested the decay of Gyrodinium aureolum either reduced oxygen levels or physically clogged faunal feeding mechanisms. Adjacent reefs were also surveyed during the same time period and the effects of the Gyrodinium aureolum bloom were less apparent. It was suggested that higher water agitation in shallow water on reefs more exposed to wave action were less affected by the phytoplankton bloom (Griffiths et al., 1979). CR.HCR.XFa.CvirCri is recorded from moderately strong-strong tidal streams (0.5-3m/sec) and at very wave exposed to moderately wave exposed sites (Connor et al., 2004). Therefore, high water movement (through wave action and/or tidal flow) could potentially cause mixing with surrounding oxygenated water (Griffiths et al., 1979) and may, therefore, decrease the effects of de-oxygenation rapidly. Sensitivity assessment. Resistance has been assessed as ‘Low’, Resilience as ‘High’. Sensitivity as ‘Low’.	Low Low NR NR Help	High Low NR NR Help	Low Low Low Low Help
Nutrient enrichment [Show more] Nutrient enrichment Benchmark. Compliance with WFD criteria for good status. Further detail Evidence This biotope is considered to be 'Not sensitive' at the pressure benchmark that assumes compliance with good status as defined by the WFD. All the characterizing species within CR.HCR.XFa.CvirCri are suspension feeders. Nutrient enrichment of coastal waters that enhances the population of phytoplankton may be beneficial in terms of an increased food supply but the effects are uncertain (Hartnoll, 1998). High primary productivity in the water column combined with high summer temperature and the development of thermal stratification (which prevents mixing of the water column) can lead to hypoxia of the bottom waters which faunal species are likely to be highly intolerant of (see de-oxygenation pressure). Johnston & Roberts (2009) conducted a meta-analysis, which reviewed 216 papers to assess how a variety of contaminants (including sewage and nutrient loading) affected 6 marine habitats (including subtidal reefs). A 30-50% reduction in species diversity and richness was identified from all habitats exposed to the contaminant types.	Not relevant (NR) NR NR NR Help	Not relevant (NR) NR NR NR Help	Not sensitive NR NR NR Help
Organic enrichment [Show more] Organic enrichment Benchmark. A deposit of 100 gC/m²/yr. Further detail Evidence All the characterizing species within CR.HCR.XFa.CvirCri are suspension feeders. Organic enrichment of coastal waters that enhances the population of phytoplankton may be beneficial to Caryophyllia smithii, Corynactis viridis and the bryozoan turf species in terms of an increased food supply but the effects are uncertain (Hartnoll, 1998). The survival of Caryophyllia smithii, Corynactis viridis and the bryozoan turf species may be influenced indirectly. High primary productivity in the water column combined with high summer temperature and the development of thermal stratification (which prevents mixing of the water column) can lead to hypoxia of the bottom waters which faunal species are likely to be highly intolerant of (see de-oxygenation pressure). Bugulina stolonifera was reported to occur in areas of the Port of Genoa harbour, heavily affected by domestic sewage pollution (Soule & Soule, 1979). Other bryozoan species within the same genus may be affected similarly. Johnston & Roberts (2009) conducted a meta-analysis, which reviewed 216 papers to assess how a variety of contaminants (including sewage and nutrient loading) affected 6 marine habitats (including subtidal reefs). A 30-50% reduction in species diversity and richness was identified from all habitats exposed to the contaminant types. Sensitivity assessment. Organic enrichment is not likely to directly negatively affect the characterizing species within this biotope, however, chronic organic enrichment may cause secondary effects such as hypoxia (refer to de-oxygenation pressure). Resistance has been assessed as ‘Low’, Resilience as ‘High’. Sensitivity as ‘Low’.	Low Low NR NR Help	High High High High Help	Low Low Low Low Help

Physical Pressures

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	Resistance	Resilience	Sensitivity
Physical loss (to land or freshwater habitat) [Show more] Physical loss (to land or freshwater habitat) Benchmark. A permanent loss of existing saline habitat within the site. Further detail Evidence All marine habitats and benthic species are considered to have a resistance of ‘None’ to this pressure and to be unable to recover from a permanent loss of habitat (resilience is ‘Very Low’). Sensitivity within the direct spatial footprint of this pressure is, therefore ‘High’. Although no specific evidence is described confidence in this assessment is ‘High’, due to the incontrovertible nature of this pressure.	None High High High Help	Very Low High High High Help	High High High High Help
Physical change (to another seabed type) [Show more] Physical change (to another seabed type) Benchmark. Permanent change from sedimentary or soft rock substrata to hard rock or artificial substrata or vice-versa. Further detail Evidence If rock were replaced with sediment, this would represent a fundamental change to the physical character of the biotope and the species would be unlikely to recover. The biotope would be lost. Sensitivity assessment. Resistance to the pressure is considered ‘None’, and resilience ‘Very low’. Sensitivity has been assessed as ‘High’.	None High High High Help	Very Low High High High Help	High High High High Help
Physical change (to another sediment type) [Show more] Physical change (to another sediment type) Benchmark. Permanent change in one Folk class (based on UK SeaMap simplified classification). Further detail Evidence Not relevant	Not relevant (NR) NR NR NR Help	Not relevant (NR) NR NR NR Help	Not relevant (NR) NR NR NR Help
Habitat structure changes - removal of substratum (extraction) [Show more] Habitat structure changes - removal of substratum (extraction) Benchmark. The extraction of substratum to 30 cm (where substratum includes sediments and soft rock but excludes hard bedrock). Further detail Evidence The species characterizing this biotope are epifauna or epiflora occurring on rock and would be sensitive to the removal of the habitat. However, extraction of rock substratum is considered unlikely and this pressure is considered to be ‘Not relevant’ to hard substratum habitats.	Not relevant (NR) NR NR NR Help	Not relevant (NR) NR NR NR Help	Not relevant (NR) NR NR NR Help
Abrasion / disturbance of the surface of the substratum or seabed [Show more] Abrasion / disturbance of the surface of the substratum or seabed Benchmark. Damage to surface features (e.g. species and physical structures within the habitat). Further detail Evidence CR.HCR.XFa.CvirCri is a subtidal biotope (Connor et al., 2004). Therefore abrasion is most likely to be a result of bottom or pot fishing gear, cable laying etc. which may cause localised mobility of the substrata and mortality of the resident community. The effect would be situation dependent however if bottom fishing gear were towed over a site it may mobilise a high proportion of the rock substrata and cause high mortality in the resident community. No relevant case studies were found on which to assess this pressure, however, Caryophyllia smithii, Corynactis viridis and bryozoans are sedentary species that might be expected to suffer from the effects of dredging. Boulcott & Howell (2011) conducted experimental Newhaven scallop dredging over a circalittoral rock habitat in the sound of Jura, Scotland and recorded the damage to the resident community. The results indicated that the sponge Pachymatisma johnstoni was highly damaged by the experimental trawl. However, only 13% of photographic samples showed visible damage to Alcyonium digitatum. Where Alcyonium digitatum damage was evident it tended to be small colonies that were ripped off the rock. The authors highlight physical damage to faunal turfs (erect bryozoans and hydroids) was difficult to quantify in the study. However, the faunal turf communities did not show large signs of damage and were only damaged by the scallop dredge teeth which was often limited in extent (approximately 2 cm wide tracts). The authors indicated that species such as Alcyonium digitatum and faunal turf communities were not as vulnerable to damage through trawling as sedimentary fauna and whilst damage to circalittoral rock fauna did occur it was of an incremental nature, with the loss of species such as Alcyonium digitatum and faunal turf communities increasing with repeated trawls. Please note, Boulcott & Howell (2011) did not mention the abrasion caused by fully loaded collection bags on the new haven dredges. A fully loaded Newhaven dredge may cause higher damage to the community than indicated in their study. Sensitivity assessment. Resistance has been assessed as ‘Medium’, resilience as ‘High’ and sensitivity as ‘Low’.	Medium High High High Help	High High High High Help	Low High High High Help
Penetration or disturbance of the substratum subsurface [Show more] Penetration or disturbance of the substratum subsurface Benchmark. Damage to sub-surface features (e.g. species and physical structures within the habitat). Further detail Evidence The species characterizing this biotope group are epifauna or epiflora occurring on rock which is resistant to subsurface penetration. The assessment for abrasion at the surface only is therefore considered to equally represent sensitivity to this pressure. This pressure is 'Not relevant' to hard rock biotopes.	Not relevant (NR) NR NR NR Help	Not relevant (NR) NR NR NR Help	Not relevant (NR) NR NR NR Help
Changes in suspended solids (water clarity) [Show more] Changes in suspended solids (water clarity) Benchmark. A change in one rank on the WFD (Water Framework Directive) scale e.g. from clear to intermediate for one year. Further detail Evidence Caryophyllia smithi, Corynactis viridisi and bryozoans are not thought highly susceptible to changes in water clarity due to the fact they are suspension feeding organisms and are not directly dependent on sunlight for nutrition. Suspension feeding organisms may be adversely affected by increases in suspended sediment, due to clogging of their feeding apparatus. Bryozoan turfs form preferentially on steep surfaces and under overhangs and larvae preferentially settle under overhangs, presumably to avoid smothering and siltation (Ryland, 1977; Hartnoll, 1983). Wendt (1998) noted that Bugula neritina grew faster on downward facing surfaces than upward facing surfaces, presumably due to siltation and reduced feeding efficiency on upward facing surfaces. But where water flow is sufficient to prevent siltation, Bugulina turbinata may colonize upward facing surfaces (Hiscock & Mitchell, 1980). Alcyonium digitatum has been shown to be tolerant of high levels of suspended sediment. Hill et al. (1997) demonstrated that Alcyonium digitatum sloughed off settled particles with a large amount of mucous. Alcyonium digitatum is also known to inhabit the entrances to sea lochs (Budd, 2008) or the entrances to estuaries (Braber & Borghouts, 1977) where water clarity is likely to be highly variable. Increased turbidity will reduce light penetration and hence phytoplankton productivity. Small phytoplankton are probably an important food source in the shallow subtidal, although, Flustra foliacea is also found at greater depths, where organic particulates (detritus) are probably more important. Sensitivity assessment. Resistance has been assessed as ‘High’, resilience as ‘High’ and sensitivity as ‘Not Sensitive’ at the benchmark level.	High High High High Help	High High High High Help	Not sensitive High High High Help
Smothering and siltation rate changes (light) [Show more] Smothering and siltation rate changes (light) Benchmark. ‘Light’ deposition of up to 5 cm of fine material added to the seabed in a single discrete event. Further detail Evidence Caryophyllia smithii, Corynactis viridis and bryozoans are sessile and thus would be unable to avoid the deposition of a smothering layer of sediment. Some Alcyonium digitatum colonies can attain a height of up to 20 cm (Edwards, 2008), so would still be able to feed in the event of sediment deposition. Caryophyllia smithii, Corynactis viridis and the bryozoan turf within CR.HCR.XFa.CvirCri are small (approx. <5 cm height from the seabed) and would therefore likely be inundated in a “light” sedimentation event. However, Bell & Turner (2000) reported Caryophyllia smithii was abundant at sites of “moderate” sedimentation (7 mm ± 0.5 mm) in Lough Hyne. It is, therefore, likely that Caryophyllia smithii would be resistant to periodic sedimentation. CR.HCR.XFa.CvirCri is recorded from moderately strong-strong tidal streams (0.5-3 m/sec) and at very wave exposed to moderately wave exposed sites (Connor et al., 2004). Therefore, water movement (through wave action and/or tidal flow) would be expected to clear 5 cm of deposited sediment within a few tidal cycles. Sensitivity assessment. Resistance has been assessed as ‘High’, and resilience as ‘High’. Sensitivity has, therefore, been assessed as ‘Not Sensitive’ at the benchmark level.	High Low NR NR Help	High High High High Help	Not sensitive Low Low Low Help
Smothering and siltation rate changes (heavy) [Show more] Smothering and siltation rate changes (heavy) Benchmark. ‘Heavy’ deposition of up to 30 cm of fine material added to the seabed in a single discrete event. Further detail Evidence Caryophyllia smithii, Corynactis viridis and bryozoans are sessile and thus would be unable to avoid the deposition of a smothering layer of sediment. Some Alcyonium digitatum colonies can attain a height of up to 20 cm (Edwards, 2008). Caryophyllia smithii, Corynactis viridis and the bryozoan turf species within CR.HCR.XFa.CvirCri are small (approx. <5 cm height from the seabed) and would, therefore, be inundated in a “heavy” sedimentation event. However, Bell & Turner (2000) reported Caryophyllia smithii was abundant at sites of “moderate” sedimentation (7mm ± 0.5mm) in Lough Hyne. It is, therefore, likely that Caryophyllia smithii would be resistant to periodic sedimentation. Suspension feeding organisms may be adversely affected by increases in suspended sediment, due to clogging of their feeding apparatus. Bryozoan turfs form preferentially on steep surfaces and under overhangs and larvae preferentially settle under overhangs, presumably to avoid smothering and siltation (Ryland, 1977; Hartnoll, 1983). Wendt (1998) noted that Bugula neritina grew faster on downward facing surfaces than upward facing surfaces, presumably due to siltation and reduced feeding efficiency on upward facing surfaces. But where water flow is sufficient to prevent siltation, Bugulina turbinata may colonize upward facing surfaces (Hiscock & Mitchell, 1980). CR.HCR.XFa.CvirCri is recorded from moderately strong-strong tidal streams (0.5-3m/sec) and at very wave exposed to moderately wave exposed sites (Connor et al., 2004). Therefore, water movement (through wave action and/or tidal flow) would be expected to clear 30 cm of deposited sediment within a few tidal cycles. Sensitivity assessment. Resistance has been assessed as ‘High’, resilience as ‘High’. Sensitivity has therefore been assessed as ‘Not Sensitive’.	High Low NR NR Help	High High High High Help	Not sensitive Low Low Low Help
Litter [Show more] Litter Benchmark. The introduction of man-made objects able to cause physical harm (surface, water column, seafloor or strandline). Further detail Evidence Not assessed.	Not Assessed (NA) NR NR NR Help	Not assessed (NA) NR NR NR Help	Not assessed (NA) NR NR NR Help
Electromagnetic changes [Show more] Electromagnetic changes Benchmark. A local electric field of 1 V/m or a local magnetic field of 10 µT. Further detail Evidence ‘No evidence’ was found.	No evidence (NEv) NR NR NR Help	Not relevant (NR) NR NR NR Help	No evidence (NEv) NR NR NR Help
Underwater noise changes [Show more] Underwater noise changes Benchmark. MSFD indicator levels (SEL or peak SPL) exceeded for 20% of days in a calendar year. Further detail Evidence None of the characterizing species within CR.HCR.XFa.CvirCri have hearing perception but vibrations may cause an impact, however, no studies exist to support an assessment.	Not relevant (NR) NR NR NR Help	Not relevant (NR) NR NR NR Help	Not relevant (NR) NR NR NR Help
Introduction of light or shading [Show more] Introduction of light or shading Benchmark. A change in incident light via anthropogenic means. Further detail Evidence CR.HCR.XFa.CvirCri is a circalittoral biotope and is thus by definition a naturally shaded environment, with low light levels. Increased shading (e.g. by the construction of a pontoon, pier etc) could be beneficial to the characterizing species within these biotopes. Sensitivity assessment. Resistance is probably 'High', with a 'High' resilience and sensitivity is assessed as 'Not Sensitive'.	High High High High Help	High High High High Help	Not sensitive High High High Help
Barrier to species movement [Show more] Barrier to species movement Benchmark. A permanent or temporary barrier to species movement over ≥50% of water body width or a 10% change in tidal excursion. Further detail Evidence Barriers and changes in tidal excursion are 'Not relevant' to biotopes restricted to open waters.	Not relevant (NR) NR NR NR Help	Not relevant (NR) NR NR NR Help	Not relevant (NR) NR NR NR Help
Death or injury by collision [Show more] Death or injury by collision Benchmark. Injury or mortality from collisions of biota with both static or moving structures due to 0.1% of tidal volume on an average tide, passing through an artificial structure. Further detail Evidence 'Not relevant' to seabed habitats. NB. Collision by grounding vessels is addressed under ‘surface abrasion’.	Not relevant (NR) NR NR NR Help	Not relevant (NR) NR NR NR Help	Not relevant (NR) NR NR NR Help
Visual disturbance [Show more] Visual disturbance Benchmark. The daily duration of transient visual cues exceeds 10% of the period of site occupancy by the feature. Further detail Evidence 'Not relevant'.	Not relevant (NR) NR NR NR Help	Not relevant (NR) NR NR NR Help	Not relevant (NR) NR NR NR Help

Biological Pressures

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	Resistance	Resilience	Sensitivity
Genetic modification & translocation of indigenous species [Show more] Genetic modification & translocation of indigenous species Benchmark. Translocation of indigenous species or the introduction of genetically modified or genetically different populations of indigenous species that may result in changes in the genetic structure of local populations, hybridization, or change in community structure. Further detail Evidence Caryophyllia smithii, Corynactis viridis and the bryozoan turf species are not cultivated or likely to be translocated. This pressure is therefore considered ‘Not relevant’.	No evidence (NEv) NR NR NR Help	Not relevant (NR) NR NR NR Help	No evidence (NEv) NR NR NR Help
Introduction or spread of invasive non-indigenous species [Show more] Introduction or spread of invasive non-indigenous species Benchmark. The introduction of one or more invasive non-indigenous species (INIS). Further detail Evidence Crepidula fornicata larvae require hard substrata for settlement. It prefers muddy gravelly, shell-rich, substrata that include gravel, or shells of other Crepidula, or other species e.g., oysters, and mussels. It is highly gregarious and seeks out adult shells for settlement, forming characteristic ‘stacks’ of adults. But it also recorded from rock, artificial substrata, and Sabellaria alveolata reefs (Blanchard, 1997, 2009; Bohn et al., 2012, 2013a, 2013b, 2015; De Montaudouin et al., 2018; Hinz et al., 2011; Helmer et al., 2019; Powell-Jennings & Calloway, 2018; Preston et al., 2020; Tillin et al., 2020). Close examination of the literature (2023) shows that evidence of its colonization and density on bedrock in the infralittoral or circalittoral was lacking. Tillin et al. (2020) suggested that Crepidula could colonize circalittoral rock due to its presence on tide-swept rough grounds in the English Channel (Hinz et al., 2011). However, Hinz et al. (2011) reported that Crepidula fornicata only dominated one assemblage (with an average of 181 individuals per trawl) on gravel substratum with boulders. Bohn et al. (2015) noted that Crepidula occurred at low density or was absent in areas dominated by boulders, and Bohn et al. (2013a, 2013b, 2015) and Preston et al. (2020) showed that while Crepidula could settle on slate panels or ‘stone’ it preferred shell, especially that of conspecifics. In addition, no evidence was found of the effect of Crepidula populations on faunal turf-dominated habitats. It was only recorded at low density (0.1-0.9/m²) in one faunal turf biotope (CR.MCR.CFaVS.CuSpH.As) (JNCC, 2015). Faunal turfs are dominated by suspension feeders so larval predation is probably high, which may prevent colonization by Crepidula. Also, faunal turf species actively compete for space and many are fast growing and opportunistic, so may out-compete Crepidula for space even if it gained a foothold in the community. Didemnum vexillum is an invasive colonial sea squirt native to Asia which was first recorded in the UK in Darthaven Marina, Dartmouth in 2005. Didemnum vexillum can form extensive mats over the substrata it colonizes; binding boulders and cobbles and altering the host habitat (Griffith et al., 2009). Didemnum vexillum can also grow over and smother the resident biological community. Recent surveys within Holyhead Marina, North Wales have found Didemnum vexillum growing on and smothering native tunicate communities (Griffith et al., 2009). Due to the rapid-re-colonization of Didemnum vexillum eradication attempts have to date failed. Presently Didemnum vexillum is isolated to several sheltered locations in the UK (NBN, 2015), however, Didemnum vexillum has successfully colonized the offshore location of the Georges Bank, USA (Lengyel et al., 2009) which is more exposed than the locations which Didemnum vexillum have colonized in the UK. It is, therefore, possible that Didemnum vexillum could colonize more exposed locations within the UK and could, therefore, pose a threat to CR.HCR.XFa.CvirCri. Sensitivity assessment. The circalittoral rock characterizing this biotope is likely to be unsuitable for the colonization by Crepidula fornicata due to the very wave exposed to moderately wave exposed conditions, in which wave action and storms may mitigate or prevent the colonization by Crepidula at high densities, although Crepidula has been recorded from areas of strong tidal streams (Hinz et al., 2011). In addition, no evidence was found of the effect of Crepidula populations on faunal turf-dominated habitats or infralittoral or circalittoral rock habitats. At present, there is 'Insufficient evidence' to suggest that the circalittoral rock biotopes are sensitive to colonization by Crepidula fornicata or other invasive species; further evidence is required.	Insufficient evidence (IEv) NR NR NR Help	Not relevant (NR) NR NR NR Help	Insufficient evidence (IEv) NR NR NR Help
Introduction of microbial pathogens [Show more] Introduction of microbial pathogens Benchmark. The introduction of relevant microbial pathogens or metazoan disease vectors to an area where they are currently not present (e.g. Martelia refringens and Bonamia, Avian influenza virus, viral Haemorrhagic Septicaemia virus). Further detail Evidence There was insufficient evidence on which to assess the sensitivity of the characterizing species within CR.HCR.XFa.CvirCri to current/known microbial pathogens. Epizooics were shown to reduce growth rates in Flustra foliacea (Stebbing, 1971a) and may have similar effects on other bryozoans. Alcyonium digitatum acts as the host for the endoparasitic species Enalcyonium forbesi and Enalcyonium rubicundum (Stock, 1988). Parasitisation may reduce the viability of a colony but not to the extent of killing them but no further evidence was found to substantiate this suggestion.	No evidence (NEv) NR NR NR Help	Not relevant (NR) NR NR NR Help	No evidence (NEv) NR NR NR Help
Removal of target species [Show more] Removal of target species Benchmark. Removal of species targeted by fishery, shellfishery or harvesting at a commercial or recreational scale. Further detail Evidence None of the characterizing species within CR.HCR.XFa.CvirCri are commercially exploited. This pressure is considered ‘Not Relevant’. Echinus esculentus was identified by Kelly & Pantazis (2001) as a species suitable for culture for the urchin Roe industry. However, no evidence could be found to suggest that significant Echinus esculentus mariculture was present in the UK. Removal of Echinus esculentus from CR.HCR.XFa.CvirCri could cause an increase in algal growth which may limit the growth of faunal species (Bell & Turner, 2000; Connor et al., 2004).	Not relevant (NR) NR NR NR Help	Not relevant (NR) NR NR NR Help	Not relevant (NR) NR NR NR Help
Removal of non-target species [Show more] Removal of non-target species Benchmark. Removal of features or incidental non-targeted catch (by-catch) through targeted fishery, shellfishery or harvesting at a commercial or recreational scale. Further detail Evidence Faunal turf communities (as in CR.HCR.XFa.CvirCri) are probably resistant to abrasion through bottom fishing (see abrasion pressure). Alcyonium digitatum goes through an annual cycle, From February to July all Alcyonium digitatum colonies are feeding, from July to November an increasing number of colonies stop feeding. During this period a large number of polyps can retract and a variety of filamentous algae, hydroids and amphipods can colonize the surface of colonies epiphytically. From December-February the epiphytic community is however sloughed off (Hartnoll, 1975). If Alcyonium digitatum were removed the epiphytic species would likely colonize rock surfaces and are therefore not dependant on Alcyonium digitatum. Within CR.HCR.XFa.CvirCri the characterising species spatially compete, however, no evidence was found to suggest other interspecific relationships or dependencies between these species. However, Corynactis viridis is a key turf forming species within this biotope, therefore, significant removal of this species would fundamentally alter the character of this biotope. Bryozoa may opportunistically colonize available space and limit successive. Sensitivity assessment. Resistance has been assessed as ‘Low’, resilience has been assessed as ’High’. Sensitivity has been assessed as ‘Low’.	Low High High High Help	High High High High Help	Low High High High Help

Bibliography

Ager, O.E.D. 2007. Alcyonidium diaphanum, Sea chervil. In Tyler-Walters H. and Hiscock K. (eds) Marine Life Information Network: Biology and Sensitivity Key Information Reviews, [on-line]. Plymouth: Marine Biological Association of the United Kingdom. Available from: http://www.marlin.ac.uk/species/detail/1738
Alexander, W., Southgate, B.A. & Bassindale, R., 1935. Survey of the River Tees: The Estuary, Chemical and Biological. HM Stationery Office.
Antoniadou, C., Voultsiadou, E. & Chintiroglou, C., 2010. Benthic colonization and succession on temperate sublittoral rocky cliffs. Journal of Experimental Marine Biology and Ecology, 382 (2), 145-153.
Ayling, A.L., 1983. Factors affecting the spatial distributions of thinly encrusting sponges from temperate waters. Oecologia, 60 (3), 412-418.
Bacescu, M.C., 1972. Substratum: Animals. In: Marine Ecology: A Comprehensive Treatise on Life in Oceans and Coastal Waters. Volume 1 Environmental Factors Part 3. (ed. O. Kinne ). Chichester: John Wiley & Sons.
Bell, J.J. & Turner, J.R., 2000. Factors influencing the density and morphometrics of the cup coral Caryophyllia smithii in Lough Hyne. Journal of the Marine Biological Association of the United Kingdom, 80, 437-441. DOI https://dx.doi.org/10.1017/S0025315400002137
Bell, J.J., 2002. Morphological responses of a cup coral to environmental gradients. Sarsia, 87, 319-330. DOI https://doi.org/10.1080/00364820260400825
Berril, N.J., 1931. Studies in tunicate development. Philosophical Transactions of the Royal Society of London (B), 219, 281-346.
Beszczynska-Möller, A., & Dye, S.R., 2013. ICES Report on Ocean Climate 2012. In ICES Cooperative Research Report, vol. 321 pp. 73.
Bishop, G.M. & Earll, R., 1984. Studies on the populations of Echinus esculentus at the St Abbs and Skomer voluntary Marine Nature Reserves. Progress in Underwater Science, 9, 53-66.
Bishop, G.M., 1985. Aspects of the reproductive ecology of the sea urchin Echinus esculentus L. Ph.D. thesis, University of Exeter, UK.
Blanchard, M., 2009. Recent expansion of the slipper limpet population (Crepidula fornicata) in the Bay of Mont-Saint-Michel (Western Channel, France). Aquatic Living Resources, 22 (1), 11-19. DOI https://doi.org/10.1051/alr/2009004
Blanchard, M., 1997. Spread of the slipper limpet Crepidula fornicata (L.1758) in Europe. Current state and consequences. Scientia Marina, 61, Supplement 9, 109-118. Available from: http://scimar.icm.csic.es/scimar/index.php/secId/6/IdArt/290/
Bohn, K., Richardson, C. & Jenkins, S., 2012. The invasive gastropod Crepidula fornicata: reproduction and recruitment in the intertidal at its northernmost range in Wales, UK, and implications for its secondary spread. Marine Biology, 159 (9), 2091-2103. DOI https://doi.org/10.1007/s00227-012-1997-3
Bohn, K., Richardson, C.A. & Jenkins, S.R., 2015. The distribution of the invasive non-native gastropod Crepidula fornicata in the Milford Haven Waterway, its northernmost population along the west coast of Britain. Helgoland Marine Research, 69 (4), 313.
Bohn, K., Richardson, C.A. & Jenkins, S.R., 2013a. Larval microhabitat associations of the non-native gastropod Crepidula fornicata and effects on recruitment success in the intertidal zone. Journal of Experimental Marine Biology and Ecology, 448, 289-297. DOI https://doi.org/10.1016/j.jembe.2013.07.020
Bohn, K., Richardson, C.A. & Jenkins, S.R., 2013b. The importance of larval supply, larval habitat selection and post-settlement mortality in determining intertidal adult abundance of the invasive gastropod Crepidula fornicata. Journal of Experimental Marine Biology and Ecology, 440, 132-140. DOI https://doi.org/10.1016/j.jembe.2012.12.008
Boolootian, R.A.,1966. Physiology of Echinodermata. (Ed. R.A. Boolootian), pp. 822. New York: John Wiley & Sons.
Boulcott, P. & Howell, T.R.W., 2011. The impact of scallop dredging on rocky-reef substrata. Fisheries Research (Amsterdam), 110 (3), 415-420.
Bower, S.M., 1996. Synopsis of Infectious Diseases and Parasites of Commercially Exploited Shellfish: Bald-sea-urchin Disease. [On-line]. Fisheries and Oceans Canada. [cited 26/01/16]. Available from: http://www.dfo-mpo.gc.ca/science/aah-saa/diseases-maladies/bsudsu-eng.html
Braber, L. & Borghouts, C.H., 1977. Distribution and ecology of Anthozoa in the estuarine region of the rivers Rhine, Meuse and Scheldt. Hydrobiologia, 52, 15-21.
Bradshaw, C., Veale, L.O., Hill, A.S. & Brand, A.R., 2000. The effects of scallop dredging on gravelly seabed communities. In: Effects of fishing on non-target species and habitats (ed. M.J. Kaiser & de S.J. Groot), pp. 83-104. Oxford: Blackwell Science.
Bryan, G.W. & Gibbs, P.E., 1991. Impact of low concentrations of tributyltin (TBT) on marine organisms: a review. In: Metal ecotoxicology: concepts and applications (ed. M.C. Newman & A.W. McIntosh), pp. 323-361. Boston: Lewis Publishers Inc.
Bryan, G.W., 1984. Pollution due to heavy metals and their compounds. In Marine Ecology: A Comprehensive, Integrated Treatise on Life in the Oceans and Coastal Waters, vol. 5. Ocean Management, part 3, (ed. O. Kinne), pp.1289-1431. New York: John Wiley & Sons.
Bucklin, A., 1987. Growth and asexual reproduction of the sea anemone Metridium: comparative laboratory studies of three species. Journal of Experimental Marine Biology and Ecology, 110, 41-52.
Budd, G.C. 2008. Alcyonium digitatum Dead man's fingers. In Tyler-Walters H. and Hiscock K. (eds) Marine Life Information Network: Biology and Sensitivity Key Information Reviews, [on-line]. Plymouth: Marine Biological Association of the United Kingdom. Available from: http://www.marlin.ac.uk/species/detail/1187
Bustamante, M., Tajadura-Martín, F.J. & Saiz-Salinas, J.I., 2010. Temporal and spatial variability on rocky intertidal macrofaunal assemblages affected by an oil spill (Basque coast, northern Spain). Journal of the Marine Biological Association of the United Kingdom, 90 (07), 1305-1317.
Carballo, J., Naranjo, S. & García-Gómez, J., 1996. Use of marine sponges as stress indicators in marine ecosystems at Algeciras Bay(southern Iberian Peninsula). Marine Ecology Progress Series, 135 (1), 109-122.
Carver, C.E., Thériault, I. & Mallet, A.L., 2010. Infection of cultured eastern oysters Crassostrea virginica by the boring sponge Cliona celata, with emphasis on sponge life history and mitigation strategies. Journal of Shellfish Research, 29 (4), 905-915.
Castège, I., Milon, E. & Pautrizel, F., 2014. Response of benthic macrofauna to an oil pollution: Lessons from the “Prestige” oil spill on the rocky shore of Guéthary (south of the Bay of Biscay, France). Deep Sea Research Part II: Topical Studies in Oceanography, 106, 192-197.
Castric-Fey, A., 1974. Les peuplements sessiles du benthos rocheux de l'archipel de Glenan (Sud-Bretagne). Ecologie descriptive and experimentale. , Ph. D. thesis, Université de Bretagne Occidentale, L' Université Paris, Paris, France.
Castric-Fey, A., 1983. Recruitment, growth and longevity of Pomatoceros triqueter and Pomatoceros lamarckii (Polychaeta, Serpulidae) on experimental panels in the Concarneau area, South Brittany. Annales de l'Institut Oceanographique, Paris, 59, 69-91.
Chomsky, O., Kamenir, Y., Hyams, M., Dubinsky, Z. & Chadwick-Furman, N., 2004. Effects of temperature on growth rate and body size in the Mediterranean Sea anemone Actinia equina. Journal of Experimental Marine Biology and Ecology, 313 (1), 63-73.
Christie, H., Jørgensen, N.M., Norderhaug, K.M. & Waage-Nielsen, E., 2003. Species distribution and habitat exploitation of fauna associated with kelp (Laminaria hyperborea) along the Norwegian coast. Journal of the Marine Biological Association of the United Kingdom, 83 (4), 687-699.
Comely, C.A. & Ansell, A.D., 1988. Invertebrate associates of the sea urchin, Echinus esculentus L., from the Scottish west coast. Ophelia, 28, 111-137.
Connor, D.W., Allen, J.H., Golding, N., Howell, K.L., Lieberknecht, L.M., Northen, K.O. & Reker, J.B., 2004. The Marine Habitat Classification for Britain and Ireland. Version 04.05. ISBN 1 861 07561 8. In JNCC (2015), The Marine Habitat Classification for Britain and Ireland Version 15.03. [2019-07-24]. Joint Nature Conservation Committee, Peterborough. Available from https://mhc.jncc.gov.uk/
Costello, M., 2001. European register of marine species: a check-list of the marine species in Europe and a bibliography of guides to their identification: Paris: Muséum national d'histoire naturelle.
Costello, M.J., Coll, M., Danovaro, R., Halpin, P., Ojaveer, H. & Miloslavich, P., 2010. A census of marine biodiversity knowledge, resources, and future challenges. Plos One, 5 (8), e12110.
Cotter, E., O’Riordan, R.M. & Myers, A.A., 2003. Recruitment patterns of serpulids (Annelida: Polychaeta) in Bantry Bay, Ireland. Journal of the Marine Biological Association of the United Kingdom, 83 (1), 41- 48. DOI https://doi.org/10.1017/S0025315403006787h
Crisp, D.J. (ed.), 1964. The effects of the severe winter of 1962-63 on marine life in Britain. Journal of Animal Ecology, 33, 165-210.
Cross, F.A., Davis, W.P., Hoss, D.E. & Wolfe, D.A., 1978. Biological Observations, Part 5. In The Amoco Cadiz Oil Spill - a preliminary scientific report (ed. W.N.Ness). NOAA/EPA Special Report, US Department of Commerce and US Environmental Protection Agency, Washington.
Danskin, G.P., 1978. Accumulation of heavy metals by some solitary tunicates. Canadian Journal of Zoology, 56 (4), 547-551.
De Kluijver, M.J., 1993. Sublittoral hard-substratum communities off Orkney and St Abbs (Scotland). Journal of the Marine Biological Association of the United Kingdom, 73 (4), 733-754.
De Montaudouin, X., Blanchet, H. & Hippert, B., 2018. Relationship between the invasive slipper limpet Crepidula fornicata and benthic megafauna structure and diversity, in Arcachon Bay. Journal of the Marine Biological Association of the United Kingdom, 98 (8), 2017-2028. DOI https://doi.org/10.1017/s0025315417001655
Diaz, R.J. & Rosenberg, R., 1995. Marine benthic hypoxia: a review of its ecological effects and the behavioural responses of benthic macrofauna. Oceanography and Marine Biology: an Annual Review, 33, 245-303.
Dons, C., 1927. Om Vest og voskmåte hos Pomatoceros triqueter. Nyt Magazin for Naturvidenskaberne, LXV, 111-126.
Dorgham, M.M., Hamdy, R., El-Rashidy, H.H. & Atta, M.M., 2013. First records of polychaetes new to Egyptian Mediterranean waters. Oceanologia, 55 (1), 235-267.
Duckworth, A.R. & Peterson, B.J., 2013. Effects of seawater temperature and pH on the boring rates of the sponge Cliona celata in scallop shells. Marine Biology, 160 (1), 27-35.
Dyrynda, P.E.J. & Ryland, J.S., 1982. Reproductive strategies and life histories in the cheilostome marine bryozoans Chartella papyracea and Bugula flabellata. Marine Biology, 71, 241-256.
Dyrynda, P.E.J., 1994. Hydrodynamic gradients and bryozoan distributions within an estuarine basin (Poole Harbour, UK). In Proceedings of the 9th International Bryozoology conference, Swansea, 1992. Biology and Palaeobiology of Bryozoans (ed. P.J. Hayward, J.S. Ryland & P.D. Taylor), pp.57-63. Fredensborg: Olsen & Olsen.
Edwards, R.V. 2008. Tubularia indivisa Oaten pipes hydroid. In Tyler-Walters H. and Hiscock K. (eds) Marine Life Information Network: Biology and Sensitivity Key Information Reviews, [on-line]. Plymouth: Marine Biological Association of the United Kingdom. Available from: http://www.marlin.ac.uk/species/detail/1967
Eggleston, D., 1972a. Patterns of reproduction in marine Ectoprocta off the Isle of Man. Journal of Natural History, 6, 31-38.
Eggleston, D., 1972b. Factors influencing the distribution of sub-littoral ectoprocts off the south of the Isle of Man (Irish Sea). Journal of Natural History, 6, 247-260.
Fariñas-Franco, J.M., Pearce, B., Porter, J., Harries, D., Mair, J.M. & Sanderson, W.G, 2014. Development and validation of indicators of Good Environmental Status for biogenic reefs formed by Modiolus modiolus, Mytilus edulis and Sabellaria spinulosa under the Marine Strategy Framework Directive. Joint Nature Conservation Committee,
Fell, P.E., Parry, E.H. & Balsamo, A.M., 1984. The life histories of sponges in the Mystic and Thames estuaries (Connecticut), with emphasis on larval settlement and postlarval reproduction. Journal of Experimental Marine Biology and Ecology, 78 (1), 127-141.
Flemer, D.A., Stanley, R.S., Ruth, B.F., Bundrick, C.M., Moody, P.H. & Moore, J.C. 1995. Recolonization of estuarine organisms - effects of microcosm size and pesticides. Hydrobiologia, 304, 85-101.
Fowler, S. & Laffoley, D., 1993. Stability in Mediterranean-Atlantic sessile epifaunal communities at the northern limits of their range. Journal of Experimental Marine Biology and Ecology, 172 (1), 109-127. DOI https://doi.org/10.1016/0022-0981(93)90092-3
Gage, J.D., 1992a. Growth bands in the sea urchin Echinus esculentus: results from tetracycline mark/recapture. Journal of the Marine Biological Association of the United Kingdom, 72, 257-260.
Gommez, J.L.C. & Miguez-Rodriguez, L.J., 1999. Effects of oil pollution on skeleton and tissues of Echinus esculentus L. 1758 (Echinodermata, Echinoidea) in a population of A Coruna Bay, Galicia, Spain. In Echinoderm Research 1998. Proceedings of the Fifth European Conference on Echinoderms, Milan, 7-12 September 1998, (ed. M.D.C. Carnevali & F. Bonasoro) pp. 439-447. Rotterdam: A.A. Balkema.
Gontar, V.I., Hop, H. & Voronkov, A.Y., 2001. Diversity and distribution of Bryozoa in Kongsfjorden, Svalbard. Polish Polar Research, 22 (3-4), 187-204.
Griffith, K., Mowat, S., Holt, R.H., Ramsay, K., Bishop, J.D., Lambert, G. & Jenkins, S.R., 2009. First records in Great Britain of the invasive colonial ascidian Didemnum vexillum Kott, 2002. Aquatic Invasions, 4 (4), 581-590. DOI https://doi.org/10.3391/ai.2009.4.4.3
Griffiths, A.B., Dennis, R. & Potts, G.W., 1979. Mortality associated with a phytoplankton bloom off Penzance in Mounts Bay. Journal of the Marine Biological Association of the United Kingdom, 59, 515-528.
Hall-Spencer, J.M. & Moore, P.G., 2000a. Impact of scallop dredging on maerl grounds. In Effects of fishing on non-target species and habitats. (ed. M.J. Kaiser & S.J., de Groot) 105-117. Oxford: Blackwell Science.
Hand, C.H., 1955. The sea anemones of central California: San Francisco University, Wasmann Biological Society.
Hansson, H., 1998. NEAT (North East Atlantic Taxa): South Scandinavian marine Echinodermata Check-List. Tjärnö Marine Biological Assocation [On-line] [cited 26/01/16]. Available from: http://www.tmbl.gu.se/libdb/taxon/neat_pdf/NEAT*Echinodermata.pdf
Hartman, W.D., 1958. Natural history of the marine sponges of southern New England. Peabody Museum of Natural History, Bulletin, 12 (12), 1-155.
Hartnoll, R.G., 1975. The annual cycle of Alcyonium digitatum. Estuarine and Coastal Marine Science, 3, 71-78.
Hartnoll, R.G., 1983. Substratum. In Sublittoral ecology. The ecology of the shallow sublittoral benthos (ed. R. Earll & D.G. Erwin), pp. 97-124. Oxford: Clarendon Press.
Hartnoll, R.G., 1998. Circalittoral faunal turf biotopes: an overview of dynamics and sensitivity characteristics for conservation management of marine SACs, Volume VIII. Scottish Association of Marine Sciences, Oban, Scotland, 109 pp. [UK Marine SAC Project. Natura 2000 reports.] Available from: http://ukmpa.marinebiodiversity.org/uk_sacs/pdfs/circfaun.pdf
Hatcher, A.M., 1998. Epibenthic colonization patterns on slabs of stabilised coal-waste in Poole Bay, UK. Hydrobiologia, 367, 153-162.
Hayward, P.J. & Ryland, J.S. (ed.), 1995. The marine fauna of the British Isles and north-west Europe. Volume 2. Molluscs to Chordates. Oxford Science Publications. Oxford: Clarendon Press.
Helmer, L., Farrell, P., Hendy, I., Harding, S., Robertson, M. & Preston, J., 2019. Active management is required to turn the tide for depleted Ostrea edulis stocks from the effects of overfishing, disease and invasive species. Peerj, 7 (2). DOI https://doi.org/10.7717/peerj.6431
Herreid, C.F., 1980. Hypoxia in invertebrates. Comparative Biochemistry and Physiology Part A: Physiology, 67 (3), 311-320. DOI https://doi.org/10.1016/S0300-9629(80)80002-8
Hill, A.S., Brand, A.R., Veale, L.O. & Hawkins, S.J., 1997. Assessment of the effects of scallop dredging on benthic communities. Final Report to MAFF, Contract CSA 2332, Liverpool: University of Liverpool
Hinz, H., Capasso, E., Lilley, M., Frost, M. & Jenkins, S.R., 2011. Temporal differences across a bio-geographical boundary reveal slow response of sub-littoral benthos to climate change. Marine Ecology Progress Series, 423, 69-82. DOI https://doi.org/10.3354/meps08963
Hiscock, K. 2000. Circalittoral caves and overhangs. In Tyler-Walters H. and Hiscock K. (eds) Marine Life Information Network: Biology and Sensitivity Key Information Reviews, [on-line]. Plymouth: Marine Biological Association of the United Kingdom. Available from: http://www.marlin.ac.uk/habitat/detail/10
Hiscock, K. & Mitchell, R., 1980. The Description and Classification of Sublittoral Epibenthic Ecosystems. In The Shore Environment, Vol. 2, Ecosystems, (ed. J.H. Price, D.E.G. Irvine, & W.F. Farnham), 323-370. London and New York: Academic Press. [Systematics Association Special Volume no. 17(b)].
Hiscock, K. & Wilson, E. 2007. Metridium senile Plumose anemone. In Tyler-Walters H. and Hiscock K. (eds) Marine Life Information Network: Biology and Sensitivity Key Information Reviews, [on-line]. Plymouth: Marine Biological Association of the United Kingdom. Available from: http://www.marlin.ac.uk/species/detail/1185
Hiscock, K., 1983. Water movement. In Sublittoral ecology. The ecology of shallow sublittoral benthos (ed. R. Earll & D.G. Erwin), pp. 58-96. Oxford: Clarendon Press.
Hiscock, K., 1985. Littoral and sublittoral monitoring in the Isles of Scilly. September 22nd to 29th, 1984. Nature Conservancy Council, Peterborough, CSD Report, no. 562., Field Studies Council Oil Pollution Research Unit, Pembroke.
Hiscock, K., Sharrock, S., Highfield, J. & Snelling, D., 2010. Colonization of an artificial reef in south-west England—ex-HMS ‘Scylla’. Journal of the Marine Biological Association of the United Kingdom, 90 (1), 69-94. DOI https://doi.org/10.1017/S0025315409991457
Hiscock, K., Southward, A., Tittley, I. & Hawkins, S., 2004. Effects of changing temperature on benthic marine life in Britain and Ireland. Aquatic Conservation: Marine and Freshwater Ecosystems, 14 (4), 333-362.
Hoare, R. & Hiscock, K., 1974. An ecological survey of the rocky coast adjacent to the effluent of a bromine extraction plant. Estuarine and Coastal Marine Science, 2 (4), 329-348.
Holme, N.A. & Wilson, J.B., 1985. Faunas associated with longitudinal furrows and sand ribbons in a tide-swept area in the English Channel. Journal of the Marine Biological Association of the United Kingdom, 65, 1051-1072.
Holt, T.J., Jones, D.R., Hawkins, S.J. & Hartnoll, R.G., 1995. The sensitivity of marine communities to man induced change - a scoping report. Countryside Council for Wales, Bangor, Contract Science Report, no. 65.
Hopkins, S.H., 1962. Distribution of species of Cliona (boring sponge) on the Eastern Shore of Virginia in relation to salinity. Chesapeake Science, 3 (2), 121-124.
Howson, C.M. & Picton, B.E., 1997. The species directory of the marine fauna and flora of the British Isles and surrounding seas. Belfast: Ulster Museum. [Ulster Museum publication, no. 276.]
Hulathduwa, Y.D. & Brown, K.M., 2006. Relative importance of hydrocarbon pollutants, salinity and tidal height in colonization of oyster reefs. Marine Environmental Research, 62 (4), 301-314.
Hyman, L.V., 1959. The Invertebrates, vol. V. Smaller coelomate groups. New York: McGraw-Hill.
Jenkins, S.R., Beukers-Stewart, B.D. & Brand, A.R., 2001. Impact of scallop dredging on benthic megafauna: a comparison of damage levels in captured and non-captured organisms. Marine Ecology Progress Series, 215, 297-301. DOI https://doi.org/10.3354/meps215297
Jensen, A.C., Collins, K.J., Lockwood, A.P.M., Mallinson, J.J. & Turnpenny, W.H., 1994. Colonization and fishery potential of a coal-ash artificial reef, Poole Bay, United Kingdom. Bulletin of Marine Science, 55, 1263-1276.
JNCC (Joint Nature Conservation Committee), 2022. The Marine Habitat Classification for Britain and Ireland Version 22.04. [Date accessed]. Available from: https://mhc.jncc.gov.uk/
Johnston, E.L. & Roberts, D.A., 2009. Contaminants reduce the richness and evenness of marine communities: a review and meta-analysis. Environmental Pollution, 157 (6), 1745-1752.
Kaiser, M.J., Ramsay, K., Richardson, C.A., Spence, F.E. & Brand, A.R., 2000. Chronic fishing disturbance has changed shelf sea benthic community structure. Journal of Animal Ecology, 69, 494-503.
Kayser, H., 1990. Bioaccumulation and transfer of cadmium in marine diatoms, Bryozoa, and Kamptozoa. In Oceanic processes in marine pollution, vol. 6. Physical and chemical processes: transport and transformation (ed. D.J. Baumgartner & I.W. Duedall), pp. 99-106. Florida: R.E. Krieger Publishing Co.
Kelly, M., Owen, P. & Pantazis, P., 2001. The commercial potential of the common sea urchin Echinus esculentus from the west coast of Scotland. Hydrobiologia, 465 (1-3), 85-94.
Keough, M.J. & Chernoff, H., 1987. Dispersal and population variation in the bryozoan Bugula neritina. Ecology, 68, 199 - 210.
Kinne, O. (ed.), 1984. Marine Ecology: A Comprehensive, Integrated Treatise on Life in Oceans and Coastal Waters.Vol. V. Ocean Management Part 3: Pollution and Protection of the Seas - Radioactive Materials, Heavy Metals and Oil. Chichester: John Wiley & Sons.
Knight-Jones, E.W. & Nelson-Smith, A., 1977. Sublittoral transects in the Menai Straits and Milford Haven. In Biology of benthic organisms (ed. B.F. Keegan, P. O Ceidigh & P.J.S. Broaden), pp. 379-390. Oxford: Pergamon Press.
Kott, P., 1985. The Australian Ascidiacea. Part I, Phlebobranchia and Stolidobranchia. Memoirs of the Queensland Museum, 23, 1-440.
Koukouras, A., 2010. Check-list of marine species from Greece. Aristotle University of Thessaloniki. Assembled in the framework of the EU FP7 PESI project.
Kukliński, P. & Barnes, D.K., 2008. Structure of intertidal and subtidal assemblages in Arctic vs temperate boulder shores. Polish Polar Research, 29 (3), 203-218.
Kupriyanova, E.K. & Badyaev, A.V., 1998. Ecological correlates of arctic Serpulidae (Annelida, Polychaeta) distributions. Ophelia, 49 (3), 181-193.
Lawrence, J.M., 1975. On the relationships between marine plants and sea urchins. Oceanography and Marine Biology: An Annual Review, 13, 213-286.
Lee, S.W. & Trott, L.B., 1973. Marine succession of fouling organisms in Hong Kong, with a comparison of woody substrates and common, locally available, anti-fouling paints. Marine Biology, 20, 101-108.
Lengyel, N.L., Collie, J.S. & Valentine, P.C., 2009. The invasive colonial ascidian Didemnum vexillum on Georges Bank - Ecological effects and genetic identification. Aquatic Invasions, 4(1), 143-152. DOI h ttps://doi.org/10.3391/ai.2009.4.1.15
Lewis, G.A. & Nichols, D., 1979a. Colonization of an artificial reef by the sea-urchin Echinus esculentus. Progress in Underwater Science, 4, 189-195.
Lyster, I., 1965. The salinity tolerance of polychaete larvae. Journal of Animal Ecology, 34 (3), 517-527.
MacBride, E.W., 1914. Textbook of Embryology, Vol. I, Invertebrata. London: MacMillan & Co.
Martin, J.P., Garese, A., Sar, A. & Acuña, F.H., 2015. Fouling community dominated by Metridium senile (Cnidaria: Anthozoa: Actiniaria) in Bahía San Julián (southern Patagonia, Argentina). Scientia Marina, 79 (2), 211-221.
Matthews, A., 1917. The development of Alcyonium digitatum with some notes on early colony formation. Quarterly Journal of Microscopial Science, 62, 43-94.
Menon, N.R., 1972. Heat tolerance, growth and regeneration in three North Sea bryozoans exposed to different constant temperatures. Marine Biology, 15, 1-11.
Migliaccio, O., Castellano, I., Romano, G. & Palumbo, A., 2014. Stress response to cadmium and manganese in Paracentrotus lividus developing embryos is mediated by nitric oxide. Aquatic Toxicology, 156, 125-134. DOI https://doi.org/10.1016/j.aquatox.2014.08.007
Mohammad, M-B.M., 1974. Effect of chronic oil pollution on a polychaete. Marine Pollution Bulletin, 5, 21-24.
Molnar, J.L., Gamboa, R.L., Revenga, C. & Spalding, M.D., 2008. Assessing the global threat of invasive species to marine biodiversity. Frontiers in Ecology and the Environment, 6 (9), 485-492.
Moore, H.B., 1937. Marine Fauna of the Isle of Man. Liverpool University Press.
Moore, P.G., 1977a. Inorganic particulate suspensions in the sea and their effects on marine animals. Oceanography and Marine Biology: An Annual Review, 15, 225-363.
Moran, P.J. & Grant, T.R., 1993. Larval settlement of marine fouling organisms in polluted water from Port Kembla Harbour, Australia. Marine Pollution Bulletin, 26, 512-514.
NBN, 2015. National Biodiversity Network 2015(20/05/2015). https://data.nbn.org.uk/
Neish, A.H. 2007. Pachymatisma johnstonia A sponge. In Tyler-Walters H. and Hiscock K. (eds) Marine Life Information Network: Biology and Sensitivity Key Information Reviews, [on-line]. Plymouth: Marine Biological Association of the United Kingdom. Available from: http://www.marlin.ac.uk/species/detail/1885
Nelson, M.L. & Craig, S.F., 2011. Role of the sea anemone Metridium senile in structuring a developing subtidal fouling community. Marine Ecology Progress Series, 421, 139-149.
Nichols, D., 1979. A nationwide survey of the British Sea Urchin Echinus esculentus. Progress in Underwater Science, 4, 161-187.
Nichols, D., 1984. An investigation of the population dynamics of the common edible sea urchin (Echinus esculentus L.) in relation to species conservation management. Report to Department of the Environment and Nature Conservancy Council from the Department of Biological Sciences, University of Exeter.
Okamura, B., 1984. The effects of ambient flow velocity, colony size and upstream colonies on the feeding success of Bryozoa, Bugula stolonifera Ryland, an arborescent species. Journal of the Experimental Marine Biology and Ecology, 83, 179-193.
Piscitelli, M., Corriero, G., Gaino, E. & Uriz, M.J., 2011. Reproductive cycles of the sympatric excavating sponges Cliona celata and Cliona viridis in the Mediterranean Sea. Invertebrate Biology, 130 (1), 1-10.
Porter, J., 2012. Seasearch Guide to Bryozoans and Hydroids of Britain and Ireland. Ross-on-Wye: Marine Conservation Society.
Powell, N., 1971. The marine bryozoa near the Panama Canal. Bulletin of Marine Science, 21 (3), 766-778.
Powell-Jennings, C. & Callaway, R., 2018. The invasive, non-native slipper limpet Crepidula fornicata is poorly adapted to sediment burial. Marine Pollution Bulletin, 130, 95-104. DOI https://doi.org/10.1016/j.marpolbul.2018.03.006
Preston, J., Fabra, M., Helmer, L., Johnson, E., Harris-Scott, E. & Hendy, I.W., 2020. Interactions of larval dynamics and substrate preference have ecological significance for benthic biodiversity and Ostrea edulis Linnaeus, 1758 in the presence of Crepidula fornicata. Aquatic Conservation: Marine and Freshwater Ecosystems, 30 (11), 2133-2149. DOI https://doi.org/10.1002/aqc.3446
Price, J.H., Irvine, D.E. & Farnham, W.F., 1980. The shore environment. Volume 2: Ecosystems. London Academic Press.
Ramos, M., 2010. IBERFAUNA. The Iberian Fauna Databank, 2015(2015/12/21). http://iberfauna.mncn.csic.es/
Rees, H.L., Waldock, R., Matthiessen, P. & Pendle, M.A., 2001. Improvements in the epifauna of the Crouch estuary (United Kingdom) following a decline in TBT concentrations. Marine Pollution Bulletin, 42, 137-144. DOI https://doi.org/10.1016/S0025-326X(00)00119-3
Rosenberg, R., Hellman, B. & Johansson, B., 1991. Hypoxic tolerance of marine benthic fauna. Marine Ecology Progress Series, 79, 127-131. DOI https://dx.doi.org/10.3354/meps079127
Ryland, J.S. & De Putron, S., 1998. An appraisal of the effects of the Sea Empress oil spillage on sensitive invertebrate communities. Countryside Council for Wales Sea Empress Contract Report, no. 285, 97pp.
Ryland, J.S., 1967. Polyzoa. Oceanography and Marine Biology: an Annual Review, 5, 343-369.
Ryland, J.S., 1970. Bryozoans. London: Hutchinson University Library.
Ryland, J.S., 1976. Physiology and ecology of marine bryozoans. Advances in Marine Biology, 14, 285-443.
Ryland, J.S., 1977. Taxes and tropisms of Bryozoans. In Biology of bryozoans (ed. R.M. Woollacott & R.L. Zimmer), pp. 411-436.
Sassaman, C. & Mangum, C., 1970. Patterns of temperature adaptation in North American Atlantic coastal actinians. Marine Biology, 7 (2), 123-130.
Schönberg, C. & Wilkinson, C., 2001. Induced colonization of corals by a clionid bioeroding sponge. Coral Reefs, 20 (1), 69-76.
SeaTemperature, 2015. World Sea Temperatures. (15/10/2015). http://www.seatemperature.org/
Segrove, F., 1941. The development of the serpulid Pomatoceros triqueta L. Quarterly Journal of Microscopical Science, 82, 467-540.
Shumway, S.E., 1978. Activity and respiration of the sea anemone, Metridium senile (L.) exposed to salinity fluctuations. Journal of Experimental Marine Biology and Ecology, 33, 85-92.
Smith, J.E. (ed.), 1968. 'Torrey Canyon'. Pollution and marine life. Cambridge: Cambridge University Press.
Snowden, E. 2007. Cliona celata A sponge. In Tyler-Walters H. and Hiscock K. (eds) Marine Life Information Network: Biology and Sensitivity Key Information Reviews, [on-line]. Plymouth: Marine Biological Association of the United Kingdom. Available from: http://www.marlin.ac.uk/species/detail/2188
Soule, D.F. & Soule, J.D., 2002. The eastern Pacific Parasmittina trispinosa complex (Bryozoa, Cheilostomatida): new and previously described species. Hancock Institute for Marine Studies, University of Southern California.
Soule, D.F. & Soule, J.D., 1979. Bryozoa (Ectoprocta). In Hart, C.W. & Fuller, S.L.H. (eds), Pollution ecology of estuarine invertebrates. New York: Academic Press, pp. 35-76.
Stebbing, A.R.D., 1971a. Growth of Flustra foliacea (Bryozoa). Marine Biology, 9, 267-273.
Stephenson, T.A., 1935. The British Sea Anemones, vol. 2. London: Ray Society.
Stock, J.H., 1988. Lamippidae (Copepoda : Siphonostomatoida) parasitic in Alcyonium. Journal of the Marine Biological Association of the United Kingdom, 68 (2), 351-359.
Svane, I. & Groendahl, F., 1988. Epibioses of Gullmarsfjorden: an underwater stereophotographical transect analysis in comparison with the investigations of Gislen in 1926-29. Ophelia, 28, 95-110.
Thomas, J.G., 1940. Pomatoceros, Sabella and Amphitrite. LMBC Memoirs on typical British marine plants and animals no.33. University Press of Liverpool. Liverpool
Tillin, H.M., Kessel, C., Sewell, J., Wood, C.A. & Bishop, J.D.D., 2020. Assessing the impact of key Marine Invasive Non-Native Species on Welsh MPA habitat features, fisheries and aquaculture. NRW Evidence Report. Report No: 454. Natural Resources Wales, Bangor, 260 pp. Available from https://naturalresourceswales.gov.uk/media/696519/assessing-the-impact-of-key-marine-invasive-non-native-species-on-welsh-mpa-habitat-features-fisheries-and-aquaculture.pdf
Tranter, P.R.G., Nicholson, D.N. & Kinchington, D., 1982. A description of spawning and post-gastrula development of the cool temperate coral, Caryophyllia smithi. Journal of the Marine Biological Association of the United Kingdom, 62, 845-854. DOI https://doi.org/10.1017/s0025315400044106
Tyler, P.A. & Young, C.M., 1998. Temperature and pressure tolerances in dispersal stages of the genus Echinus (Echinodermata: Echinoidea): prerequisites for deep sea invasion and speciation. Deep Sea Research II, 45 (1), 253-277. DOI https://doi.org/10.1016/S0967-0645(97)00091-X
Tyler-Walters, H., 2005. Laminaria hyperborea with dense foliose red seaweeds on exposed infralittoral rock. Marine Life Information Network: Biology and Sensitivity Key Information Sub-programme [on-line]: Plymouth: Marine Biological Association of the United Kingdom. 2015(20/05/2015). http://www.marlin.ac.uk/habitatsbasicinfo.php?habitatid=171&code=1997
Tyler-Walters, H., 2008. Echinus esculentus. Edible sea urchin. Marine Life Information Network: Biology and Sensitivity Key Information Sub-programme [on-line]. [cited 26/01/16]. Plymouth: Marine Biological Association of the United Kingdom. Available from: http://www.marlin.ac.uk/species/detail/1311
Tyler-Walters, H. & Ballerstedt, S., 2007. Flustra foliacea Hornwrack. In Tyler-Walters H. and Hiscock K. (eds) Marine Life Information Network: Biology and Sensitivity Key Information Reviews, [on-line]. Plymouth: Marine Biological Association of the United Kingdom. Available from: http://www.marlin.ac.uk/species/detail/1609
Tyler-Walters, H., 2008b. Corallina officinalis Coral weed. In Tyler-Walters H. and Hiscock K. (eds) Marine Life Information Network: Biology and Sensitivity Key Information Reviews, [on-line]. Plymouth: Marine Biological Association of the United Kingdom. Available from: http://www.marlin.ac.uk/species/detail/1364
Ursin, E., 1960. A quantitative investigation of the echinoderm fauna of the central North Sea. Meddelelser fra Danmark Fiskeri-og-Havundersogelser, 2 (24), pp. 204.
Veale, L.O., Hill, A.S., Hawkins, S.J. & Brand, A.R., 2000. Effects of long term physical disturbance by scallop fishing on subtidal epifaunal assemblages and habitats. Marine Biology, 137, 325-337.
Walsh, P. & Somero, G., 1981. Temperature adaptation in sea anemones: physiological and biochemical variability in geographically separate populations of Metridium senile. Marine Biology, 62 (1), 25-34.
Warburton, F.E., 1966. The behavior of sponge larvae. Ecological Society of America, 47 (4), 672-674.
Wendt, D.E., 1998. Effect of larval swimming duration on growth and reproduction of Bugula neritina (Bryozoa) under field conditions. Biological Bulletin, 195, 126-135.
Whomersley, P. & Picken, G., 2003. Long-term dynamics of fouling communities found on offshore installations in the North Sea. Journal of the Marine Biological Association of the UK, 83 (5), 897-901.
Williams, R., 1997. Actinothoe sphyrodeta (Cnidaria, Actiniaria): the first records from Portugal and the Mediterranean Sea. Journal of the Marine Biological Association of the United Kingdom, 77 (1), 245-248.
Wood, C., 2007. Seasearch Observer's Guide to Marine Life of Britain and Ireland, Ross-on-Wye: Marine Conservation Society.
Wood, E. (ed.), 1988. Sea Life of Britain and Ireland. Marine Conservation Society. IMMEL Publishing, London
Wood. C., 2005. Seasearch guide to sea anemones and corals of Britain and Ireland. Ross-on-Wye: Marine Conservation Society.
Zintzen, V., Norro, A., Massin, C. & Mallefet, J., 2008a. Temporal variation of Tubularia indivisa (Cnidaria, Tubulariidae) and associated epizoites on artificial habitat communities in the North Sea. Marine Biology, 153 (3), 405-420.

Citation

This review can be cited as:

Stamp, T.E., Lloyd, K.A., & Watson, A., 2023. Corynactis viridis and a mixed turf of crisiids, Bugula, Scrupocellaria, and Cellaria on moderately tide-swept exposed circalittoral rock. In Tyler-Walters H. Marine Life Information Network: Biology and Sensitivity Key Information Reviews, [on-line]. Plymouth: Marine Biological Association of the United Kingdom. [cited 27-12-2024]. Available from: https://marlin.ac.uk/habitat/detail/272

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Last Updated: 30/11/2023

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Sensitivity assessments

Sensitivity evidence

Corynactis viridis and a mixed turf of crisiids, Bugula, Scrupocellaria, and Cellaria on moderately tide-swept exposed circalittoral rock

Corynactis viridis and a mixed turf of crisiids, Bugula, Scrupocellaria, and Cellaria on moderately tide-swept exposed circalittoral rock

Corynactis viridis and a mixed turf of crisiids, Bugula, Scrupocellaria, and Cellaria on moderately tide-swept exposed circalittoral rock

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