The Marine Life Information Network

Temperature increase (local)

Benchmark. A 5°C increase in temperature for one month, or 2°C for one year. Further detail

Evidence

Hughes (1998a) suggested that in shallow sea lochs, sedimentary biotopes would probably experience a seasonal temperature range between about 5-15 °C. Greater temperature extremes may be experienced in unusually warm summers or cold winters, although the effects on sedimentary communities is unknown (Hughes, 1998a). Burrowing species would probably be able to avoid extreme temperatures within the sediment so that epifauna were likely to be more vulnerable.

Ocnus planci and Ocnus brunneus reach their northern limit in northern Europe and the British Isles. Ocnus brunneus is reported from France and Denmark while Ocnus planci is reported from the Mediterranean and Senegal. Therefore, they are unlikely to be adversely affected by a long-term temperature rise. Similarly, most other dominant species within the biotope are found to the south of the British Isles and unlikely to be affected adversely by long-term temperature rise. The growth and fecundity of Amphiura filiformis may increase with increased average temperatures while Ophiothrix fragilis was reported to recruit in high numbers after mild winters (see MarLIN reviews).

Overall, most species in the biotope are unlikely to be adversely affected by long-term temperature rise and are buffered from extremes of temperature by their depth. Therefore, a resistance of High has been recorded to represent effects on growth rates and metabolism. Therefore, resilience is High and the biotope is assessed as Not sensitive at the benchmark level. In shallow, isolated waters (e.g. sea lochs) increased summer temperatures may result in stratification of the water column (a thermocline) and increased oxygen demand resulting in deoxygenation of the bottom waters (Hughes, 1998a)(see  deoxygenation below).

Temperature decrease (local)

Benchmark. A 5°C decrease in temperature for one month, or 2°C for one year. Further detail

Evidence

Ocnus planci and Ocnus brunneus reach their northern limit in British waters, however, no information on their temperature tolerance was found. Most of the other common species within the biotope are recorded north of British and Irish waters and are unlikely to be affected by long-term decreases in temperature. However, shallow waters population may be more vulnerable to low temperatures in extreme winters (Hughes, 1998a). For example, a population of Amphiura filiformis at 27 m depth off the Danish coast was killed by the winter of 1962-63 (Muus, 1981) and a population at 35-50 m depth in the inner German Bight was killed in the winter of 1969-1970 and a new population did not re-establish until 1974 (Gerdes, 1976). Ursin (cited in Gerdes, 1978) suggested that Amphiura filiformis did not occur in areas with winter temperatures below 4°C although in Helgoland waters it can tolerate temperatures as low as 3.5°C. Low temperatures are a limiting factor for breeding in this species, which takes place during the warmest months in the British waters. Similarly, Ophiothrix fragilis occurs in shallow, enclosed waters that regularly drop to 3 °C but is absent from areas where temperatures drop to 0°C. In addition, temperature influences growth and reproduction in many species of hydroids and ascidians (see species reviews).

Overall, most species will probably not be adversely affected by a long-term decrease in temperatures, although short-term acute decreases in temperatures associated with extreme winters may result in loss of a few species. Therefore, resilience is High and the biotope is assessed as Not sensitive at the benchmark level.

Salinity increase (local)

Benchmark. A increase in one MNCR salinity category above the usual range of the biotope or habitat. Further detail

Evidence

Echinoderms are generally regarded as stenohaline and most species are exclusively marine (Binyon, 1966; Pawson, 1966; Stickle & Diehl, 1987; Lawrence, 1996, Russell, 2013). An increase in salinity at the benchmark level would result in a salinity of >40 psu, and as hypersaline water is likely to sink to the seabed, the biotope may be affected by hypersaline effluents. Roberts et al. (2010b) suggested that hypersaline effluent dispersed quickly but was more of a concern at the seabed and in areas of low energy where widespread alternations in the community of soft sediments were observed. In several studies, echinoderms and ascidians were amongst the most sensitive groups examined (Roberts et al., 2010b).

Sensitivity assessment. An increase in salinity from full to >40 psu is probably detrimental to the important characteristic species of the biotope. Although, there is no direct evidence of the effects of hypersaline water, the stenohaline nature of the echinoderm dominated community suggests that hypersaline conditions may cause mortality. Therefore, a resistance of Low is recorded but at Low confidence. Resilience would probably be Medium so that sensitivity may be Medium.

Salinity decrease (local)

Benchmark. A decrease in one MNCR salinity category above the usual range of the biotope or habitat. Further detail

Evidence

Echinoderms are generally regarded as stenohaline and most species are exclusively marine (Binyon, 1966; Pawson, 1966; Stickle & Diehl, 1987; Lawrence, 1996, Russell, 2013). Lawrence (1996) cited several examples of mass mortalities in echinoderms due to sudden increases in river discharge or localized heavy rains. However, some euryhaline species have been reported and local adaptation may occur in some species (see Binyon, 1966 and Stickle & Diehl, 1987 for reviews). A decrease in salinity from e.g. full to reduced for a year (see benchmark) is likely to result in marked changes in community composition, including loss of the Ocnus aggregations. Therefore, a resistance of None has been suggested.  Resilience is probably Medium so that sensitivity is assessed as Medium.

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 biotope is only found in areas of weak or very weak tidal streams and so a decrease in flow is unlikely but it is likely to be intolerant of increases in water flow.  Some tidal flow is necessary for the supply of food in the form of organic particles by resuspension and advective transport, gaseous exchange and the removal of wastes, influencing the growth rate of suspension-feeding benthos (Dauwe, 1998).  Ocnus planci has been recorded from moderately strong to very weak tidal streams (Connor et al., 1997b). The feeding efficiency of suspension feeding species may be impaired in strong flow, while allowing other species to colonize.

An increase in water flow will probably result in a marked change in the community due to modification of the substratum, removing finer particulates such as muds and favouring the deposition of coarser deposits. The resultant sediment scour may adversely affect epifaunal species. Increased water flow may also cause small stones, pebbles, and cobbles to roll along the substratum resulting in further abrasion for epifauna.  

Sensitivity assessment.  A significant increase in water flow may winnow away the mud surface or even remove the mud habitat and hence the biotope if prolonged. An increase of 0.2 m/s may begin to erode the mud surface where the site is already subject to flow (e.g. weak flow at the seabed), based on sediment erosion deposition curves (Wright, 2001). However, the dominant suspension feeding echinoderms position themselves on the stones, shells and rocks on the surface of the muddy substratum, and may not be affected adversely by an increase of 0.1-0.2 m/s. Therefore, a resistance of High is recorded but with Low confidence. Therefore, resilience is probably High so that the biotope is assessed as Not sensitive at the benchmark level.  

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

The pressure benchmark is relevant only to littoral and shallow sublittoral fringe biotopes.

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

Ocnus planci was recorded from moderately wave exposed to extremely wave sheltered habitats (Connor et al., 1997b). But this biotope (IFiMu.Ocn) is only recorded from moderately wave exposed to extremely wave sheltered conditions. An increase in wave exposure and the resultant increase in oscillatory water movement at the sediment surface is likely to resuspend fine particulates, and deposit coarser sediment types, e.g. sands and gravels resulting in loss of many of the mud dwelling species. Water movement is also likely to roll, or move stones, cobbles , pebbles and shell fragments, resulting in increased sediment scour and abrasion, and probably loss of many of the epifaunal species. Ocnus species may survive on coarser substrata but are rare in wave exposed environments (Connor et al., 1997b). Overall, the community is likely to change significantly and the aggregations of Ocnus lost.  However, a change of 0.3-0.5% of significant wave height (the benchmark) is unlikely to be significant, especially at depth. Therefore, a resistance of High is suggested so that resilience also High and the biotope is assessed as Not sensitive at the benchmark level.

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.

Bryan (1984) reported that early work had shown that echinoderm larvae were sensitive to heavy metals, e.g. the intolerance of larvae of Paracentrotus lividus to copper (Cu) had been used to develop a water quality assessment. Kinne (1984) reported developmental disturbances in Echinus esculentus exposed to waters containing 25 µg / l of copper (Cu) and heavy metals caused reproductive anomalies in the starfish Asterias rubens (Besten, et al., 1989, 1991). Sea-urchins, especially the eggs and larvae, are used for toxicity testing and environmental monitoring (reviewed by Dinnel et al. 1988). Crompton (1997) reported that mortalities occurred in echinoderms after 4-14 day exposure to above 10-100 µg/l Cu, 1-10 mg/l Zn and 10-100 mg/l Cr but that mortalities occurred in echinoderm larvae above10-100 µg/ l Ni.

Various heavy metals have been show to have sublethal effects on growth in the few hydroids studied experimentally (Stebbing, 1981; Bryan, 1984; Ringelband, 2001). Gastropod molluscs have been reported to relatively tolerant of heavy metals while a wide range of sublethal and lethal effects have been observed in larval and adult crustaceans (Bryan, 1984). Bryan (1984) suggested that polychaetes are fairly resistant to heavy metals, based on the species studied. Short-term toxicity in polychaetes was highest to Hg, Cu and Ag, declined with Al, Cr, Zn and Pb whereas Cd, Ni, Co and Se the least toxic.

Tri-butyl tin (TBT) has a marked effect on numerous marine organisms (Bryan & Gibbs, 1991). Bryan & Gibbs (1991) reported that virtually no hydroids were present on hard bottom communities in TBT contaminated sites and suggested that some hydroids were intolerant of TBT levels between 100 and 500 ng/l. Copepod and mysid crustaceans were particularly intolerant of TBT while crabs were more resistant (Bryan & Gibbs, 1991), although recent evidence suggests some sublethal endocrine disruption in crabs. The effect of TBT on Nucella lapillus and other neogastropods is well known (see review), and similar effects on reproduction may occur in other gastropod molluscs, including nudibranchs. Rees et al. (2001) reported that the abundance of epifauna had increased in the Crouch estuary in the five years since TBT was banned from use on small vessels. Rees et al. (2001) suggested that TBT inhibited settlement in ascidian larvae. This report suggests that epifaunal species (including, bryozoan, hydroids and ascidians) may be at least inhibited by the presence of TBT.

Overall, while some invertebrate groups are tolerant, many of the other groups, including echinoderms are probably intolerant, especially their larvae.

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.

Sheltered embayments and lagoons, where this biotope is found, are particularly vulnerable to oil pollution, which may settle onto the sediment and persist for years (Cole et al., 1999). Subsequent digestion or degradation of the oil by microbes may result in nutrient enrichment and eutrophication (see nutrients below). Although protected from direct smothering by oil by its depth, the biotope is relatively shallow and would be exposed to the water soluble fraction of oil, water soluble PAHs, and oil adsorbed onto particulates.

Suchanek (1993) reviewed the effects of oil spills on marine invertebrates and concluded that, in general, on soft sediment habitats, infaunal polychaetes, bivalves and amphipods were particularly affected. Crude oil and refined oils were shown to have little effect on fertilization in sea urchin eggs but in the presence of dispersants fertilization was poor and embryonic development was impaired (Johnston, 1984). Sea urchin eggs showed developmental abnormalities when exposed to 10-30 mg/l of hydrocarbons and crude oil : Corexit dispersant mixtures have been shown to cause functional loss of tube feet and spines in sea urchins (Suchanek, 1993). Olsgard & Gray (1995) found the brittlestar Amphiura filiformis to be very sensitive to oil pollution. During monitoring of sediments in the Ekofisk oilfield, Addy et al. (1978) suggest that reduced abundance of Amphiura filiformis within 2-3 km of the site was related to discharges of oil from the platforms and to physical disturbance of the sediment. Although acute toxicity test showed that drill cuttings containing oil based muds had a very low toxicity (LC50 52,800 ppm total hydrocarbons in test sediment), Newton & McKenzie (1998) suggest these are a poor predictor of chronic response. Chronic sub-lethal effects were detected around the Beryl oil platform in the North Sea where the levels of oil in the sediment were very low (3 ppm) and Amphiura filiformis was excluded from areas nearer the platform with higher sediment oil content. Similarly, in Ophiothrix fragilis, exposure to 30,000 ppm oil reduces its load of symbiotic bacteria by 50% and brittle stars begin to die (Newton & McKenzie, 1995). Crude oil from the Torrey Canyon and the detergent used to disperse it caused mass mortalities of echinoderms; Asterias rubens, Echinocardium cordatum, Psammechinus miliaris, Echinus esculentus, Marthasterias glacialis and Acrocnida brachiata (Smith, 1968).

Suchanek (1993) reported that the anemones Anthopleura spp. and Actinia spp. survived in waters exposed to spills and chronic inputs of oils. Similarly, one month after the Torrey Canyon oil spill the dahlia anemone, Urticina felina, was found to be one of the most resistant animals on the shore, being commonly found alive in pools between the tide-marks which appeared to be devoid of all other animals (Smith, 1968). If the physiology within different animals groups can be assumed to be similar, then amphipods, echinoderms, and soft corals may be intolerant of hydrocarbon contamination while hydroids may demonstrate sublethal effects and anemones and some species of sponge are relatively tolerant.

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.

Little information on the toxicity of synthetic chemicals to holothurians was found. Newton & McKenzie (1995) suggested that echinoderms tend to be very intolerant of various types of marine pollution but gave no detailed information. Cole et al. (1999) reported that echinoderm larvae displayed adverse effects when exposed to 0.15mg/l of the pesticide Dichlorobenzene (DCB). Smith (1968) demonstrated that 0.5 -1 ppm of the detergent BP1002 resulted in developmental abnormalities in echinopluteus larvae of Echinus esculentus. Smith (1968) also noted that large numbers of dead Echinus esculentus were found between 5.5 and 14.5 m in the vicinity of Sennen, presumably due to a combination of wave exposure and heavy spraying of dispersants in that area. TBT was shown to inhibit arm regeneration in the brittlestar Ophioderma brevispina, at 10ng/l and produce significant inhibition at 100 ng/l. It was suggested that TBT acts via the nervous system, although direct action on the tissues at the point of breakage could not be excluded (Bryan & Gibbs, 1991) Therefore, holothurians and their larvae may also be intolerant of synthetic chemicals.

The species richness of hydroid communities decreases with increasing pollution (Boero, 1984; Gili & Hughes, 1995). Alcyonium digitatum at a depth of 16m in the locality of Sennen Cove (Pedu-men-du, Cornwall) died resulting from the offshore spread and toxic effect of detergents e.g. BP 1002 sprayed along the shoreline to disperse oil from the Torrey Canyon tanker spill (Smith, 1986). Possible sub-lethal effects of exposure to synthetic chemicals may result in a change in morphology, growth rate or disruption of the reproductive cycle.

Therefore, hydroids, crustaceans, gastropods, and ascidians are probably intolerant of TBT contamination. Echinoderms, including Ocnus, may be intolerant of synthetic chemicals.

Radionuclide contamination

Benchmark. An increase in 10µGy/h above background levels. Further detail

Evidence

No evidence was found

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.

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

Lawrence (1996) reported mass mortality of echinoderms in the Gulf of Trieste due to hypoxia caused by a strong thermocline combined with high pelagic productivity and eutrophication. The brittlestar Ophiura quinquemaculata was killed with a few days, and holothurians including Ocnus planci (as Cucumaria planci), starfish Asteropecten sp. and the remaining brittlestars were killed within a week. In experiments, Amphiura filiformis only left its protected position in the sediment when oxygen levels fell below 0.85mg/l (Rosenberg et al., 1991). Mass mortality of Amphiura filiformis was observed during severely low oxygen events (<0.7 mg/l) (Nilsson, 1999). However, at oxygen concentrations between 0.85 mg/l and 1.0 mg/l Rosenberg et al. (1991) observed the species was able to survive for several weeks. Echinoderms were shown to be intolerant of the effects of algal blooms, resulting in mortalities of the sea urchins Echinus esculentus and Paracentrotus lividus, and the holothurian Labidoplax digitata amongst other echinoderms, probably due to hypoxia caused by death of the algal bloom algae (Boalch, 1979; Forster, 1979; Griffiths et al., 1979; Lawrence, 1996). Diaz & Rosenberg (1995, Figure 5)) suggested that shrimp and crustaceans were lost as oxygen levels dropped below ca 0.75 ml/l and that the macroinfauna was reduced below ca 0.4ml/l. Vaquer-Sunyer & Duarte (2008) suggested a median sublethal oxygen concentration of 1.22 mg O₂/l (± 0.25) for a number of echinoderms reviewed in their study. Echinoderms were neither the most or the least sensitive of the taxonomic groups examined.  Riedel et al. (2012) examined the effects of hypoxia and anoxia on macrofauna in the North Adriatic, using in situ experimental apparatus.  The concluded that, decapods, echinoderms and polychaetes were amongst the most sensitive to hypoxia while ascidians and anthozoans were amongst the most resistant of the species encountered in their study. However, Ocnus planci survived moderate (<0.8 ml O₂/l, <1.12 mg O₂/l) to severe (<0.5 ml O₂/l, <0.7 mg O₂/l) hypoxia but died with several hours (median duration of 23.3 hrs) of anoxic conditions; anoxia was reached after 48 hrs of the onset of the experiment (Riedel et al., 2012).

Overall, based on the evidence cited above, echinoderms appear to be intolerant of hypoxic conditions. However, Ocnus planci may be amongst the most resistant of those studied by Riedel et al. (2012) in their 3 to 4 day experiment. Therefore, a decrease in oxygen levels to below 2 mg O₂ /l for a week is likely to result in loss of most of the suspension feeding echinoderms and a proportion of the Ocnus spp. population, based on the observation in the Gulf of Trieste, and a resistance of Low is suggested. Resilience is probably Medium so that sensitivity is assessed as Medium.

Nutrient enrichment

Benchmark. Compliance with WFD criteria for good status. Further detail

Evidence

Hughes (1998a) suggested that sea loch sediments, where this biotope occurs, were naturally rich in organic matter. Moderate enrichment is likely to increase food availability and hence, the abundance of deposit feeding organisms. Increases in nutrients and low oxygen conditions result in anaerobic conditions within the sediment. Nutrient enrichment may also result in algal blooms. For example Cerianthus lloydii was found near the centre of sewage sludge dumping groups at ca 10% organic carbon but more abundant at intermediate nutrient enrichment (Hughes, 1998a) and echinoderms were shown to be intolerant of the effects of algal blooms, resulting in mortalities of the sea urchins Echinus esculentus and Paracentrotus lividus, and the holothurian Labidoplax digitata amongst other echinoderms, probably due to hypoxia caused by death of the algal bloom algae (Boalch, 1979; Forster, 1979; Griffiths et al., 1979; Lawrence, 1996). Therefore, while moderate enrichment may be beneficial, echinoderms are indirectly intolerant due to sudden hypoxia resulting from the death of algal blooms.  

Nevertheless, the biotope is assessed as Not sensitive at the pressure benchmark that assumes compliance with good status as defined by the WFD.

Organic enrichment

Benchmark. A deposit of 100 gC/m²/yr. Further detail

Evidence

Hughes (1998a) suggested that sea loch sediments, where this biotope occurs, were naturally rich in organic matter. Moderate enrichment is likely to increase food availability and hence, the abundance of deposit feeding organisms.

Cerianthus lloydii was found near the centre of sewage sludge dumping groups at ca 10% organic carbon but was more abundant at intermediate nutrient enrichment (Hughes, 1998b). But Borja et al. (2000) and Gittenberger and van Loon (2011) both assigned Cerianthus lloydii to their Ecological Group I, ‘species very sensitive to organic enrichment and present under unpolluted conditions (initial state)’ in of the AZTI Marine Biotic Index (AMBI) index to assess disturbance (including organic enrichment). The basis for their assessment and relation to the pressure benchmark is not clear.

However, no information on the effects of organic enrichment on Ocnus planci was found.

Sensitivity assessment. In the absence of direct evidence, it is assumed that muddy habitats in sea lochs are probably naturally rich in organic matter (Hughes, 1998a).  Therefore, a resistance of High is suggested with Low confidence. Hence, resilience is High and the biotope assessed as Not sensitive at the benchmark level.

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.

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

This biotope (IFiMu.Ocn) is an epifaunal overlay on an otherwise sedimentary biotope. The important charactersitic epifauna (Ocnus planci) position themsleves on stones, pebbles shells and other hard substrata to avail themsleves of the passing current. Other suspension feeding brittlestar may do the same.  Yet the biotope is only recorded on muddy habitats with stones and shell on the surface (Connor et al., 2004).  If sedimentary substrata were replaced with rock substrata the biotope would be lost, as it would not longer be a sedimentary habitat and no longer recognised under the habitat clasification.

Sensitivity assessment. Resistance to the pressure is considered ’None‘, and resilience ’Very low‘ or ‘None’ (as the pressure represents a permanent change) and the sensitivity of this biotope is assessed as ’High’.

Physical change (to another sediment type)

Benchmark. Permanent change in one Folk class (based on UK SeaMap simplified classification). Further detail

Evidence

This biotope (IFiMu.Ocn) is an epifaunal overlay on an otherwise sedimentary biotope. The important characteristic epifauna (Ocnus planci) position themselves on stones, pebbles, shells, and other hard substrata to avail themselves of the passing current. Other suspension-feeding brittlestars may do the same. Yet the biotope is only recorded on muddy habitats with stones and shells on the surface (Connor et al., 2004).  It is unknown why the aggregations of suspension-feeding echinoderms occur in this habitat. But a change in sediment type by one Folk class to, for example, muddy sand or sand, would result in the loss of the biotope as described under the habitat classification.  

Sensitivity assessment. Resistance to the pressure is assessed as ’None‘, and resilience as ’Very low‘ or ‘None’ (as the pressure represents a permanent change) and the sensitivity of this biotope is assessed as ’High’.

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

This biotope (IFiMu.Ocn) is an epifaunal overlay on an otherwise sedimentary biotope. The important characteristic epifauna (Ocnus planci) position themselves on stones, pebbles shells, and other hard substrata to avail themselves of the passing current. Other suspension feeding brittlestars may do the same. The extraction of the sediment to a depth of 30 cm would remove the mud infauna and the surface epifauna with the affected area.  Therefore, a resistance of None is suggested based on expert judgement. Resilience is probably Medium so that the sensitivity is assessed as Medium.  

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

Stable sedimentary habitats, such as mud were amongst the most vulnerable to fishing activities, e.g. otter board trawling (Ball et al., 2000b; Collie et al., 2000). Tracks left by otter boards were visible 18 months after experimental trawls in Gareloch (Ball et al., 2000b). Ball et al., (2000b) concluded that trawling modified the benthic community due to an increase in opportunistic polychaetes. However, Kaiser et al. (2006) concluded that otter boards had a significant initial effect on muddy sands and muds, but that the effects were short-lived in mud habitats.

Erect epifaunal species are particularly vulnerable to physical disturbance (Jennings & Kaiser, 1998). Hydroids are likely to be detached or damaged by bottom trawling or dredging (Holt et al., 1995). Veale et al. (2000) reported that the abundance, biomass, and production of epifaunal assemblages decreased with increasing fishing effort. Hydroid and bryozoan matrices were reported to be greatly reduced in fished areas (Jennings & Kaiser, 1998). Mobile gears also result in modification of the substratum, including the removal of shell debris, cobbles and rocks, and the movement of boulders (Bullimore, 1985; Jennings & Kaiser, 1998) on which many of the species in this community depend. The removal of rocks or boulders to which species are attached results in substratum loss (see above). For example, Magorrian & Service (1998) reported that queen scallop trawling flattened horse mussel beds and removed emergent epifauna in Strangford Lough. They suggested that the emergent epifauna such as Alcyonium digitatum, a frequent component of this biotope, were more sensitive than the horse mussels themselves and reflected early signs of damage. Species with fragile tests such as Echinus esculentus and the brittlestar Ophiocomina nigra and edible crabs Cancer pagurus were reported to suffer badly from the impact of a passing scallop dredge (Bradshaw et al., 2000). But brittlestars such as Ophiothrix fragilis probably have good powers of regeneration and infaunal species such as Amphiura filiformis may avoid the effects of a passing beam trawl. Scavengers such as Asterias rubens and Buccinum undatum were reported to be fairly robust to encounters with trawls (Kaiser & Spencer, 1995) may benefit in the short-term, feeding on species damaged or killed by passing dredges. However, Veale et al. (2000) did not detect any net benefit at the population level. Greathead et al. (2011) were not able to conclude if the variation in Cerianthus abundance in the Fladden Grounds was due to miscounting, its patchy distribution, or fishing activity.

Ocnus species are the most important characterizing species within the biotope and may be damaged by physical disturbance due to an anchor or passing fishing gear. But they probably have good powers of regeneration (given their fissiparous habit) and would survive if the damage were not too severe. However, they may be displaced due to physical abrasion as the stones and shells they occupy are moved, rolled, or removed from the habitat.

Sensitivity assessment. Overall, physical disturbance by an anchor or mobile fishing gear is likely to remove a significant proportion of the epifauna within the community and attract scavengers to the community in the short term. Therefore, a resistance of Low is suggested. Resilience is probably Medium so sensitivity is assessed as Medium.

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

Sensitivity assessment. Based on the evidence present under abrasion above physical disturbance by mobile fishing gear is likely to remove a significant proportion of the epifauna within the community and attract scavengers to the community in the short-term. Therefore, a resistance of Low is suggested. Resilience is probably Medium so that sensitivity is assessed as Medium.

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

The biotope occurs in sheltered areas, in fine sediments, subject to high suspended sediment loads. The effect of increased deposition of fine silt is uncertain but it is possible that feeding structures may become clogged.  However, Ocnus planci (as Cucumaria planci) maintained a high filtration efficiency even at food concentrations (suspension densities) three times average natural levels (Ölsher & Fedra, 1977). Burrowing species are unlikely to be affected and suspension feeding species are likely to experience, and hence tolerate, periodic re-suspension of suspended sediment due to wave or current surges, storms or digging by predators. Therefore, they are likely to tolerate an increase in suspended sediment for a month, although feeding efficiency of some species, especially epifaunal suspension feeders, may be impaired.  Therefore, a resistance of High is suggested.  Hence, resilience is High and the biotope is assessed as Not sensitive at the benchmark level.

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

Deposition of a 5 cm layer of sediment is unlikely to disturb burrowing infaunal species. Kukert & Smith (1992) noted that deposition of 5-6 cm of sediment resulted in a 32% reduction in macrofaunal abundance in less than 1 month but that deposit feeders had returned to background levels within 3 months, while scavengers and carnivores took longer. Suspension feeding epifauna are likely to be the least resistant. Species that project above the sediment surface, such as sea pens and Sabella pavonina are probably tall enough to avoid the effects, while burrowing species such as Myxicola infundibulum, Chaetopterus variopedatus, Cerianthus lloydii and Amphiura filiformis could probably burrow up through the sediment. For example, in normal accretion, Cerianthus lloydii keeps pace with the accretion and, as a result, develops burrows much larger than the animal itself (Schäfer, 1972; Bromley, 2012). Schäfer (1972) reported that an increase in depositional rate led to an avoidance behaviour in Cerianthus lloydii. The organism ceases tube building activity and instead the animal bunches its tentacles and intrudes its way up to the new surface, where it establishes a new burrow. However, no information on the depth of material through which is can burrow was given

Other epifauna e.g. hydroids, tubeworms, ascidians are fixed to the substratum, the brittlestar Ophiothrix fragilis and smaller sea urchins are unable to burrow effectively and would probably be smothered, potentially succumbing due to clogged respiratory apparatus and temporary anoxia.

At up to 15 cm in length, Ocnus planci may be large enough to avoid the effects of smothering but Ocnus brunneus is a small species. However, holothurians are generally burrowing species and it is probably able to regain the sediment surface rapidly. Raised areas of sediment may even provide this species with a new feeding perch.

Sensitvity assessment. Ocnus and most of the species typical of mud communities would probably survive smothering by 5 cm of sediment. However, some epifaunal species, and juveniles of several species may be affected adversely, resulting in a short-term decrease in species richness. Therefore, a resistance of High is suggested.  Hence, resilience is High and the biotope is assessed as Not sensitive at the benchmark level.

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

Deposition of 30 cm of fine sediment is likely to smother the entire community. In the sheltered low energy environment this biotope occurs, the sediment is likely to remain. Therefore, the effect on the community will depend on the ability of the species to burrow through the deposited sediment.  Small brittlestars and hydroids or ascidians affixed to stones and shell will be unable to burrow, while large burrowing species such as Chaetopterus variopedatus and Cerianthus lloydii may be able to regain the surface. For example, in normal accretion, Cerianthus lloydii keeps pace with the accretion and, as a result, develops burrows much larger than the animal itself (Schäfer, 1972; Bromley, 2012). Schäfer (1972) reported that an increase in depositional rate led to an avoidance behaviour in Cerianthus lloydii. The organism ceases tube building activity and instead the animal bunches its tentacles and intrudes its way up to the new surface, where it establishes a new burrow. However, no information on the depth of material through which is can burrow was given.

At up to 15 cm in length, Ocnus planci may be large enough to avoid the effects of smothering but Ocnus brunneus is a small species. However, holothurians are generally burrowing species and it is probably able to regain the sediment surface rapidly. Raised areas of sediment may even provide this species with a new feeding perch. But the stones and shell typical of the biotope would also be smothered and lost and with them the epifaunal perches they provide. As a result, the aggregations of Ocnus spp. that typify this biotope may also be lost, although the reason for their aggregation is unknown.

Sensitivity assessment. Smothering by 30 cm of sediment is likely to result in the loss of smaller species and epifauna while larger burrowing species may survive.  Therefore, a resistance of Medium is suggested to represent the loss of some of the Ocnus population and other epifauna. The resilience is probably High so that sensitivity is assessed as Low.

Litter

Benchmark. The introduction of man-made objects able to cause physical harm (surface, water column, seafloor or strandline). Further detail

Evidence

Not assessed.

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.

Underwater noise changes

Benchmark. MSFD indicator levels (SEL or peak SPL) exceeded for 20% of days in a calendar year. Further detail

Evidence

Some of the characterizing species associated with this biotope, in particular, the epifauna, may respond to sound vibrations. Feeding will resume once the disturbing factor has passed. Therefore, this pressure is probably Not relevant in this biotope.

Introduction of light or shading

Benchmark. A change in incident light via anthropogenic means. Further detail

Evidence

Epifaunal suspension feeders that feed on passing seston such as phytoplankton and a variety of marine organic particulates dominate the biotope.  Most of the productivity is probably secondary and not directly dependent on the availability of light , especially in the deeper examples of the biotope.  Therefore, this biotope is probably Not sensitive to changes in light (resistance and resilience are High).

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

Not relevant – this pressure is considered applicable to mobile species, e.g. fish and marine mammals rather than seabed habitats. Physical and hydrographic barriers may limit the dispersal of seed or propagules.  But seed or propagule dispersal is not considered under the pressure definition and benchmark.

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. 

Visual disturbance

Benchmark. The daily duration of transient visual cues exceeds 10% of the period of site occupancy by the feature. Further detail

Evidence

Most species within the biotope are burrowing and have no or poor visual perception and are unlikely to be affected by visual disturbance such as shading. Epifauna such as crabs have well developed visual acuity and are likely to respond to movement in order to avoid predators. However, it is unlikely that the species will be affected by visual disturbance at the benchmark level.

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

No evidence of genetic modification, breeding, or translocation was found.

Introduction or spread of invasive non-indigenous species

Benchmark. The introduction of one or more invasive non-indigenous species (INIS). Further detail

Evidence

The American slipper limpet Crepidula fornicata was introduced to the UK and Europe in the 1870s from the Atlantic coasts of North America with imports of the eastern oyster Crassostrea virginica. It was recorded in Liverpool in 1870 and the Essex coast in 1887-1890. It has spread through expansion and introductions along the full extent of the English Channel and into the European mainland (Blanchard, 1997, 2009; Bohn et al., 2012, 2013a, 2013b, 2015; De Montaudouin et al., 2018; Hinz et al., 2011; McNeill et al., 2010; Powell-Jennings & Calloway, 2018; Preston et al., 2020; Stiger-Pouvreau & Thouzeau, 2015).

Crepidula fornicata is recorded from shallow, sheltered bays, lagoons and estuaries or the sheltered sides of islands, in variable salinity (18 to 40) although it prefers ca 30 (Tillin et al., 2020). 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 in a wide variety of habitats including clean sands, artificial substrata, Sabellaria alveolata reefs and areas subject to moderately strong tidal streams (Blanchard, 1997, 2009; Bohn et al., 2012, 2013a, 2013b, 2015; De Montaudouin et al., 2018; Hinz et al., 2011; Powell-Jennings & Calloway, 2018; Preston et al., 2020; Stiger-Pouvreau & Thouzeau, 2015; Tillin et al., 2020). 

High densities of Crepidula fornicata cause ecological impacts on sedimentary habitats. The species can form dense carpets that can smother the seabed in shallow bays, changing and modifying the habitat structure. At high densities, the species physically smothers the sediment, and the resultant build-up of silt, pseudofaeces, and faeces is deposited and trapped within the bed (Tillin et al., 2020, Fitzgerald, 2007, Blanchard, 2009, Stiger-Pouvreau & Thouzeau, 2015). The biodeposition rates of Crepidula are extremely high and once deposited, form an anoxic mud, making the environment suitable for other species, including most infauna (Stiger-Pouvreau & Thouzeau, 2015, Blanchard, 2009). For example, in fine sands, the community is replaced by a reef of slipper limpets, that provide hard substrata for sessile suspension-feeders (e.g., sea squirts, tube worms and fixed shellfish), while mobile carnivorous microfauna occupy species between or within shells, resulting in a homogeneous Crepidula dominated habitat (Blanchard, 2009). Blanchard (2009) suggested the transition occurred and became irreversible at 50% cover of the limpet. De Montaudouin et al. (2018) suggested that homogenization occurred above a threshold of 20-50 Crepidula /m². 

Impacts on the structure of benthic communities will depend on the type of habitat that Crepidula colonizes. De Montaudouin & Sauriau (1999) reported that in muddy sediment dominated by deposit-feeders, species richness, abundance and biomass increased in the presence of high densities of Crepidula (ca 562 to 4772 ind./m²), in the Bay of Marennes-Oléron, presumably because the Crepidula bed provided hard substrata in an otherwise sedimentary habitat. In medium sands, Crepidula density was moderate (330-1300 ind./m²) but there was no significant difference between communities in the presence of Crepidula. Intertidal coarse sediment was less suitable for Crepidula with only moderate or low abundances (11 ind./m²) and its presence did not affect the abundance or diversity of macrofauna. However, there was a higher abundance of suspension–feeders and mobile Crustacea in the absence of Crepidula (De Montaudouin & Sauriau, 1999). The presence of Crepidula as an ecosystem engineer has created a range of new niche habitats, reducing biodiversity as it modifies habitats (Fitzgerald, 2007). De Montaudouin et al. (1999) concluded that Crepidula did not influence macroinvertebrate diversity or density significantly under experimental conditions, on fine sands in Arcachon Bay, France. De Montaudouin et al. (2018) noted that the limpet reef increased the species diversity in the bed, but homogenised diversity compared to areas where the limpets were absent. In the Milford Haven Waterway (MHW), the highest densities of Crepidula were found in areas of sediment with hard substrata, e.g., mixed fine sediment with shell or gravel or both (grain sizes 16-256 mm) but, while Crepidula density increased as gravel cover increased in the subtidal, the reverse was found in the intertidal (Bohn et al., 2015). Bohn et al. (2015) suggested that high densities of Crepidula in high-energy environments were possible in the subtidal but not the intertidal, suggesting the availability of this substratum type is beneficial for its establishment. Hinz et al. (2011) reported a substantial increase in the occurrence of Crepidula off the Isle of Wight, between 1958 and 2006, at a depth of ca 60 m, on hard substrata (gravel, cobbles, and boulders), swept by strong tidal streams. Presumably, Crepidula is more tolerant of tidal flow than the oscillatory flow caused by wave action which may be less suitable (Tillin et al., 2020). 

Sternapsis scutata is a non-native polychaete that has extended its range in inshore muddy sediments in the southwest of the UK (Shelley et al., 2008). However, in mesocosm experiments, little effect on biological functioning was detected after the introduction of the polychaete and a doubling of its biomass (Shelley et al., 2008).

Sensitivity assessment. The above evidence suggests that Crepidula fornicata could colonize this habitat due to the presence of stones and shells, and the lack of wave action. Therefore, Crepidula has the potential to colonize, and modify the habitat and its associated community due to the introduction of Crepidula shell biomass, silt, pseudofaeces and faeces (Blanchard, 2009; Tillin et al., 2020).  The aggregations of Ocnus sp. that characterize this biotope occur due to the presence of stones and shells, on which the aggregations develop.  Therefore, Crepidula could compete with Ocnus for that substratum and potentially exclude Ocnus. Alternatively, Ocnus may be able to use stacks of Crepidula to raise themselves into the currents for feeding. However, there is no information on the potential interaction between Crepidula and suspension-feeding sea cucumbers and dense beds of Crepidula may or may not exclude Ocnus. Therefore, resistance is assessed as 'Low' on the assumption that Crepidula could reach medium to high abundances in this habitat, and modify the sediment and habitat so that it is no longer suitable for aggregations of Ocnus, albeit with 'Low' confidence.  Resilience is assessed as 'Very low' as it would require the removal of Crepidula probably by artificial means. Hence, sensitivity is assessed as 'High'. However, Crepidula has not yet been reported to occur in this biotope so the confidence in the assessment is 'Low' and further evidence is required. 

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

The gastropod snail Melanella alba parasites holothurians, probably by sucking their fluids (Graham, 1988) and has been recorded in this biotope (Connor et al., 2004). Any parasite is likely to reduce the viability of the host species, so a resistance of High has been recorded. Therefore, resilience is also High and the biotope is assessed as Not sensitive.

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 this biotope are currently directly targeted in the UK and, hence, this pressure is considered to be Not relevant.

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

The physical effects of fisheries or dredging activities are addressed under abrasion, penetration and extraction pressures above. No clear biological relationships between the important characteristic species were found. Therefore, removal of any one species may not affect other members of the community adversely.  However, is the important characterizing species were removed as by-catch, the character of the biotope would change. A significant decline in the abundance of either Ocnus planci would result in loss of the biotope as recognised by the habitat classification.  Therefore, a resistance of Medium is recorded, albeit at Low confidence. As resilience is probably High, sensitivity is assessed as Low.