The Marine Life Information Network

Under the middle emission, high emission and extreme scenarios, sea surface temperatures are expected to increase by 3, 4 and 5°C respectively, leading to temperatures increasing to between 22-24°C by the end of this century in the south of the UK, although northern UK temperatures will be up to 5°C lower. Species from the genus Bathyporeia spp. have high upper lethal temperature limits (the temperature at which 50% of individuals died after 24 hours exposure) of 37.5°C for Bathyporeia pilosa and 33.4°C for Bathyporeia pelagica (Preece, 1971). The ability to withstand these high temperatures may be because they can be found in the intertidal, where temperatures fluctuate much more than the subtidal, where conditions are more stable. While they can withstand a short-term, sharp temperature increase, their ability to withstand long-term changes in temperature is more difficult to discern. Most species of Bathyporeia (Bathyporeia pelagica, Bathyporeia elegans, Bathyporeia sarsi) have a limited distribution, being primarily found around the UK, and from the coast of Norway down to the French coast of the Bay of Biscay, and are abundant in the North Sea (Künitzer et al., 1992).

Nephtys cirrosa has a less limited, and more southern distribution than amphipods from the genus Bathyporeia spp. and is therefore more likely to exhibit greater temperature tolerance. It is common in the NE Atlantic, including the English Channel and the North Sea and down the coast of Spain and Portugal, and can also be found in the Mediterranean and the Black Sea down to a depth of 45 m (Rainer, 1991).

Sensitivity assessment. With sea surface temperatures around the UK currently falling between 6-19°C (Huthnance, 2010), populations of Nephtys cirrosa and Bathyporeia spp. are likely to be able to adapt to cope with a gradual rise in ocean temperatures of 3°C (middle emission scenario), leading to mean summer high temperatures of 22°C by the end of this century, as these species currently experience summer temperatures of 22°C in the Bay of Biscay (Koutsikopoulos et al., 1998). Therefore, for the middle emission scenario, resistance is assessed as ‘High’, and resilience as ‘High’, and sensitivity is assessed as ‘Not sensitive’

Under the high emission and extreme scenarios, whereby summer sea surface temperatures are expected to increase 4-5°C to 23-24°C in southern England, there is likely to be some impact on Bathyporeia spp. although Nephtys cirrosa is expected to be able to withstand this temperature rise, as its distribution includes the Mediterranean, where these temperatures are exceeded. Whilst Bathyporeia spp. have been known to withstand short-term extreme temperature fluctuations (Preece, 1971), species from the genus Bathyporeia are known to have a more limited geographical distribution, and occur north of the Bay of Biscay where summer temperatures reach 22°C (Koutsikopoulos et al., 1998), which suggests that this may be a cut off point for proliferation of this species. An increase of 4-5°C is likely to cause some mortality and loss to populations in southern England (an increase in temperature of 4-5°C in Scotland, Northern England, Wales or Ireland would lead to temperatures of 22°C), resistance is assessed as ‘Medium’, and resilience is assessed as ‘Very Low’ as any population declines in southern England will not recover due to the long-term nature of global warming. Therefore, this biotope is assessed as ‘Medium’ sensitivity to both the high emission and extreme scenarios.

Under the middle emission, high emission and extreme scenarios, sea surface temperatures are expected to increase by 3, 4 and 5°C respectively, leading to temperatures increasing to between 22-24°C by the end of this century in the south of the UK, although northern UK temperatures will be up to 5°C lower. Species from the genus Bathyporeia spp. have high upper lethal temperature limits (the temperature at which 50% of individuals died after 24 hours exposure) of 37.5°C for Bathyporeia pilosa and 33.4°C for Bathyporeia pelagica (Preece, 1971). The ability to withstand these high temperatures may be because they can be found in the intertidal, where temperatures fluctuate much more than the subtidal, where conditions are more stable. While they can withstand a short-term, sharp temperature increase, their ability to withstand long-term changes in temperature is more difficult to discern. Most species of Bathyporeia (Bathyporeia pelagica, Bathyporeia elegans, Bathyporeia sarsi) have a limited distribution, being primarily found around the UK, and from the coast of Norway down to the French coast of the Bay of Biscay, and are abundant in the North Sea (Künitzer et al., 1992).

Nephtys cirrosa has a less limited, and more southern distribution than amphipods from the genus Bathyporeia spp. and is therefore more likely to exhibit greater temperature tolerance. It is common in the NE Atlantic, including the English Channel and the North Sea and down the coast of Spain and Portugal, and can also be found in the Mediterranean and the Black Sea down to a depth of 45 m (Rainer, 1991).

Sensitivity assessment. With sea surface temperatures around the UK currently falling between 6-19°C (Huthnance, 2010), populations of Nephtys cirrosa and Bathyporeia spp. are likely to be able to adapt to cope with a gradual rise in ocean temperatures of 3°C (middle emission scenario), leading to mean summer high temperatures of 22°C by the end of this century, as these species currently experience summer temperatures of 22°C in the Bay of Biscay (Koutsikopoulos et al., 1998). Therefore, for the middle emission scenario, resistance is assessed as ‘High’, and resilience as ‘High’, and sensitivity is assessed as ‘Not sensitive’

Under the high emission and extreme scenarios, whereby summer sea surface temperatures are expected to increase 4-5°C to 23-24°C in southern England, there is likely to be some impact on Bathyporeia spp. although Nephtys cirrosa is expected to be able to withstand this temperature rise, as its distribution includes the Mediterranean, where these temperatures are exceeded. Whilst Bathyporeia spp. have been known to withstand short-term extreme temperature fluctuations (Preece, 1971), species from the genus Bathyporeia are known to have a more limited geographical distribution, and occur north of the Bay of Biscay where summer temperatures reach 22°C (Koutsikopoulos et al., 1998), which suggests that this may be a cut off point for proliferation of this species. An increase of 4-5°C is likely to cause some mortality and loss to populations in southern England (an increase in temperature of 4-5°C in Scotland, Northern England, Wales or Ireland would lead to temperatures of 22°C), resistance is assessed as ‘Medium’, and resilience is assessed as ‘Very Low’ as any population declines in southern England will not recover due to the long-term nature of global warming. Therefore, this biotope is assessed as ‘Medium’ sensitivity to both the high emission and extreme scenarios.

Under the middle emission, high emission and extreme scenarios, sea surface temperatures are expected to increase by 3, 4 and 5°C respectively, leading to temperatures increasing to between 22-24°C by the end of this century in the south of the UK, although northern UK temperatures will be up to 5°C lower. Species from the genus Bathyporeia spp. have high upper lethal temperature limits (the temperature at which 50% of individuals died after 24 hours exposure) of 37.5°C for Bathyporeia pilosa and 33.4°C for Bathyporeia pelagica (Preece, 1971). The ability to withstand these high temperatures may be because they can be found in the intertidal, where temperatures fluctuate much more than the subtidal, where conditions are more stable. While they can withstand a short-term, sharp temperature increase, their ability to withstand long-term changes in temperature is more difficult to discern. Most species of Bathyporeia (Bathyporeia pelagica, Bathyporeia elegans, Bathyporeia sarsi) have a limited distribution, being primarily found around the UK, and from the coast of Norway down to the French coast of the Bay of Biscay, and are abundant in the North Sea (Künitzer et al., 1992).

Nephtys cirrosa has a less limited, and more southern distribution than amphipods from the genus Bathyporeia spp. and is therefore more likely to exhibit greater temperature tolerance. It is common in the NE Atlantic, including the English Channel and the North Sea and down the coast of Spain and Portugal, and can also be found in the Mediterranean and the Black Sea down to a depth of 45 m (Rainer, 1991).

Sensitivity assessment. With sea surface temperatures around the UK currently falling between 6-19°C (Huthnance, 2010), populations of Nephtys cirrosa and Bathyporeia spp. are likely to be able to adapt to cope with a gradual rise in ocean temperatures of 3°C (middle emission scenario), leading to mean summer high temperatures of 22°C by the end of this century, as these species currently experience summer temperatures of 22°C in the Bay of Biscay (Koutsikopoulos et al., 1998). Therefore, for the middle emission scenario, resistance is assessed as ‘High’, and resilience as ‘High’, and sensitivity is assessed as ‘Not sensitive’

Under the high emission and extreme scenarios, whereby summer sea surface temperatures are expected to increase 4-5°C to 23-24°C in southern England, there is likely to be some impact on Bathyporeia spp. although Nephtys cirrosa is expected to be able to withstand this temperature rise, as its distribution includes the Mediterranean, where these temperatures are exceeded. Whilst Bathyporeia spp. have been known to withstand short-term extreme temperature fluctuations (Preece, 1971), species from the genus Bathyporeia are known to have a more limited geographical distribution, and occur north of the Bay of Biscay where summer temperatures reach 22°C (Koutsikopoulos et al., 1998), which suggests that this may be a cut off point for proliferation of this species. An increase of 4-5°C is likely to cause some mortality and loss to populations in southern England (an increase in temperature of 4-5°C in Scotland, Northern England, Wales or Ireland would lead to temperatures of 22°C), resistance is assessed as ‘Medium’, and resilience is assessed as ‘Very Low’ as any population declines in southern England will not recover due to the long-term nature of global warming. Therefore, this biotope is assessed as ‘Medium’ sensitivity to both the high emission and extreme scenarios.

Marine heatwaves due to increased air-sea heat flux are predicted to occur more frequently, last for longer and at increased intensity by the end of this century under both middle and high emission scenarios (Frölicher et al., 2018). Both Bathyporeia pilosa and Bathyporeia pelagica are known to be able to withstand short-term high temperatures, with upper lethal temperatures after 24 hrs for both species exceeding 33°C, and no mortality observed at 29°C (Preece, 1971).

In Kiel Fjord in the Baltic Sea, where temperatures generally range from 0-20°C, simulated marine heatwaves on natural communities (summer temperature increased to 25°C), led to increased biomass in two out of four species of polychaetes, whilst a decrease in both biomass and abundance was seen for a tube-dwelling polychaete (Pansch et al., 2018). In the same study, the biomass of two of the four amphipod species significantly increased, whereas no significant negative impacts were seen on either biomass or abundance of the other species. The southern limit of Gammarus salinus is the Bay of Biscay, and this species has a similar distribution to species from the genus Bathyporeia. Gammarus salinus appeared to have a slight positive response in abundance and biomass to a simulated heatwave of 25°C, although this was not significant (Pansch et al., 2018).

Sensitivity assessment. Under the middle emission scenario, if heatwaves occurred every three years, with a maximum intensity of 2°C for a period of 80 days by the end of this century, this could lead to summer sea temperatures reaching up to 24°C in southern England. It is likely that both Nephtys cirrosa and Bathyporeia spp. will be able to withstand a heatwave of this intensity and duration, as Nephtys cirrosa can withstand Mediterranean temperatures and Gammarus salinus, which has a similar geographical range as Bathyporeia spp. can withstand heatwaves of this magnitude. Therefore, resistance is assessed as ‘High’, resilience as ‘High’, and the biotope is assessed as ‘Not sensitive’. Under the high emission scenario, if heatwaves occur every two years by the end of this century, reaching a maximum intensity of 3.5°C for 120 days, this could lead to the heatwave lasting the entire summer with temperatures reaching up to 26.5°C. Nephtys cirrosa will likely be able to withstand this temperature. Although species from the genus Bathyporeia are known to be able to withstand high temperatures for short periods (Preece, 1971), they do not occur south of the Bay of Biscay and some mortality is likely during a prolongued three-month heatwave event. As such, under the high emission scenario, resistance has been assessed as ‘Medium’. As recovery of Bathyporeia spp. populations is rapid, resilience is assessed as ‘High’.  Therefore, this biotope is assessed as having ‘Low’ sensitivity to marine heatwaves under the high emission scenario. 

Marine heatwaves due to increased air-sea heat flux are predicted to occur more frequently, last for longer and at increased intensity by the end of this century under both middle and high emission scenarios (Frölicher et al., 2018). Both Bathyporeia pilosa and Bathyporeia pelagica are known to be able to withstand short-term high temperatures, with upper lethal temperatures after 24 hrs for both species exceeding 33°C, and no mortality observed at 29°C (Preece, 1971).

In Kiel Fjord in the Baltic Sea, where temperatures generally range from 0-20°C, simulated marine heatwaves on natural communities (summer temperature increased to 25°C), led to increased biomass in two out of four species of polychaetes, whilst a decrease in both biomass and abundance was seen for a tube-dwelling polychaete (Pansch et al., 2018). In the same study, the biomass of two of the four amphipod species significantly increased, whereas no significant negative impacts were seen on either biomass or abundance of the other species. The southern limit of Gammarus salinus is the Bay of Biscay, and this species has a similar distribution to species from the genus Bathyporeia. Gammarus salinus appeared to have a slight positive response in abundance and biomass to a simulated heatwave of 25°C, although this was not significant (Pansch et al., 2018).

Sensitivity assessment. Under the middle emission scenario, if heatwaves occurred every three years, with a maximum intensity of 2°C for a period of 80 days by the end of this century, this could lead to summer sea temperatures reaching up to 24°C in southern England. It is likely that both Nephtys cirrosa and Bathyporeia spp. will be able to withstand a heatwave of this intensity and duration, as Nephtys cirrosa can withstand Mediterranean temperatures and Gammarus salinus, which has a similar geographical range as Bathyporeia spp. can withstand heatwaves of this magnitude. Therefore, resistance is assessed as ‘High’, resilience as ‘High’, and the biotope is assessed as ‘Not sensitive’. Under the high emission scenario, if heatwaves occur every two years by the end of this century, reaching a maximum intensity of 3.5°C for 120 days, this could lead to the heatwave lasting the entire summer with temperatures reaching up to 26.5°C. Nephtys cirrosa will likely be able to withstand this temperature. Although species from the genus Bathyporeia are known to be able to withstand high temperatures for short periods (Preece, 1971), they do not occur south of the Bay of Biscay and some mortality is likely during a prolongued three-month heatwave event. As such, under the high emission scenario, resistance has been assessed as ‘Medium’. As recovery of Bathyporeia spp. populations is rapid, resilience is assessed as ‘High’.  Therefore, this biotope is assessed as having ‘Low’ sensitivity to marine heatwaves under the high emission scenario. 

Increasing levels of CO₂ in the atmosphere have led to the average pH of sea surface waters dropping from 8.25 in the 1700s to 8.14 in the 1990s (Jacobson, 2005). There is no direct evidence of the impact of ocean acidification on either Nephtys cirrosa or amphipods from the genus Bathyporeia, which characterize this habitat. Amphipods are generally thought to be less sensitive to ocean acidification than some other taxa and are actually found in greater numbers at naturally CO₂ enriched vents (Kroeker et al., 2011, Garrard et al., 2014, Vizzini et al., 2017). This increase in abundance is not directly related to CO₂ enrichment, but rather due to indirect effects such as reduced predation or increased food supply.  A laboratory study found that under CO₂ enrichment, the population size of the amphipod Gammarus locusta increased 20 fold and the proportion of gravid females doubled, suggesting that ocean acidification may confer an advantage to amphipods by relaxing environmental constraints on reproduction (Heldt et al., 2016). Further laboratory experiments show little effect of ocean acidification at levels expected for the high emission scenario at the end of this century (pH 7.8) (Hauton et al., 2009, Hale et al., 2011, Lim & Harley, 2018).

Non-calcifying polychaetes are also thought to be less sensitive than many other taxa.  When non-calcifying polychaetes were transplanted from control to low pH areas, they showed evidence of either adaptation or acclimation to their conditions (Calosi et al., 2013). There is some evidence that sperm may be affected by ocean acidification at levels expected in the high emission scenario, with percentage sperm motility (Schlegel et al., 2014) and sperm velocity (Campbell et al., 2014) decreasing in the polychaetes Galeolaria caespitosa and Arenicola marina, leading to a decrease in sperm fertility success (Campbell et al., 2014). Reduced sperm fertility and hence recruitment, may lead to some population-level effects. However, at natural CO₂ vents, the abundance of polychaetes either remained the same (Kroeker et al., 2011) or increased (Garrard et al., 2014, Vizzini et al., 2017). Most species of polychaetes generally exhibit high fecundity and are free spawning (Ramirez-Llodra, 2002), which may help them maintain population levels, even with a decrease in fertilization success. For example, Nephtys cirrosa is a reasonably fecund species that releases between 10,000 – 80,000 eggs into the water column during a spawning cycle (MES, 2010).

Sensitivity Assessment. Direct evidence of the impact of ocean acidification on Nephtys cirrosa and Bathyporeia spp. is lacking. However, in general, non-calcifying polychaetes and amphipods appear to be tolerant. Therefore, it is likely that the characterizing species of this biotope will show a ‘High’ resistance to a decrease in pH, even though ocean acidification has been shown to lead to negative impacts on polychaete fertilization success under experimental conditions (Campbell et al., 2014, Schlegel et al., 2014). As such, based on the evidence available, under both the middle and high emission scenarios the biotope is assessed as ‘High’ resistance to ocean acidification, and ‘High’ resilience, leading to an assessment of ‘Not sensitive’ at the benchmark level

Increasing levels of CO₂ in the atmosphere have led to the average pH of sea surface waters dropping from 8.25 in the 1700s to 8.14 in the 1990s (Jacobson, 2005). There is no direct evidence of the impact of ocean acidification on either Nephtys cirrosa or amphipods from the genus Bathyporeia, which characterize this habitat. Amphipods are generally thought to be less sensitive to ocean acidification than some other taxa and are actually found in greater numbers at naturally CO₂ enriched vents (Kroeker et al., 2011, Garrard et al., 2014, Vizzini et al., 2017). This increase in abundance is not directly related to CO₂ enrichment, but rather due to indirect effects such as reduced predation or increased food supply.  A laboratory study found that under CO₂ enrichment, the population size of the amphipod Gammarus locusta increased 20 fold and the proportion of gravid females doubled, suggesting that ocean acidification may confer an advantage to amphipods by relaxing environmental constraints on reproduction (Heldt et al., 2016). Further laboratory experiments show little effect of ocean acidification at levels expected for the high emission scenario at the end of this century (pH 7.8) (Hauton et al., 2009, Hale et al., 2011, Lim & Harley, 2018).

Non-calcifying polychaetes are also thought to be less sensitive than many other taxa.  When non-calcifying polychaetes were transplanted from control to low pH areas, they showed evidence of either adaptation or acclimation to their conditions (Calosi et al., 2013). There is some evidence that sperm may be affected by ocean acidification at levels expected in the high emission scenario, with percentage sperm motility (Schlegel et al., 2014) and sperm velocity (Campbell et al., 2014) decreasing in the polychaetes Galeolaria caespitosa and Arenicola marina, leading to a decrease in sperm fertility success (Campbell et al., 2014). Reduced sperm fertility and hence recruitment, may lead to some population-level effects. However, at natural CO₂ vents, the abundance of polychaetes either remained the same (Kroeker et al., 2011) or increased (Garrard et al., 2014, Vizzini et al., 2017). Most species of polychaetes generally exhibit high fecundity and are free spawning (Ramirez-Llodra, 2002), which may help them maintain population levels, even with a decrease in fertilization success. For example, Nephtys cirrosa is a reasonably fecund species that releases between 10,000 – 80,000 eggs into the water column during a spawning cycle (MES, 2010).

Sensitivity Assessment. Direct evidence of the impact of ocean acidification on Nephtys cirrosa and Bathyporeia spp. is lacking. However, in general, non-calcifying polychaetes and amphipods appear to be tolerant. Therefore, it is likely that the characterizing species of this biotope will show a ‘High’ resistance to a decrease in pH, even though ocean acidification has been shown to lead to negative impacts on polychaete fertilization success under experimental conditions (Campbell et al., 2014, Schlegel et al., 2014). As such, based on the evidence available, under both the middle and high emission scenarios the biotope is assessed as ‘High’ resistance to ocean acidification, and ‘High’ resilience, leading to an assessment of ‘Not sensitive’ at the benchmark level

Sea-level rise is occurring through a combination of thermal expansion and ice melt.  Sea levels have risen 1-3 mm/yr in the last century (Cazenave & Nerem, 2004, Church et al., 2004, Church & White, 2006). The most recent projections on sea-level rise suggest a rise of 50 cm under the middle emission scenario, 70 cm under the high emission scenario, and 107 cm under the extreme scenario. Species from the genus Bathyporeia and Nephtys cirrosa are abundant at on the Dogger Bank, which has a depth range of 15- 36 m (Wieking & Kröncke, 2003), suggesting that, as long as the habitat remains the same (sand), these species will be tolerant of future sea-level rise for all three scenarios. Nephtys cirrosa occurs on clean sand, down to a depth of 45 m (Rainer, 1991), whilst species of Bathyporeia are often abundant at depths <30 m (Künitzer et al., 1992)

Any potential increase in wave exposure in relation to sea-level rise (e.g. Fujii & Raffaelli, 2008) is not expected to impact this biotope, as these species occur on medium to very fine sand in moderately exposed to exposed areas (JNCC, 2019), therefore an increase in exposure is unlikely to change habitat classification.  However, as wave action is reduced with depth, an increase in depth may stabilize the sediment allowing the habitat to transition into IMuSaFfabMag, resulting in loss of the deeper portions of the biotope. However, over time the biotope may extend inshore, depending on location. Sensitivity assessment. There is likely to be considerable variation between sites, and the depth range occupied by the biotope.  Hence, it is difficult to assess the effect of the different sea-level rise scenarios.  As the biotope can occur from 0-10 m in depth, it is assumed that a sea-level rise of 50 cm, or 70 cm (middle to high emission scenarios) would have limited effect but that a 107 cm rise (the extreme scenario) might result in loss of part of the deeper extent of the biotope in some sites.  Therefore, resistance is assessed as ‘High’ under the middle and high emission scenarios so that resilience is ‘High’ and sensitivity assessed as ‘Not sensitive’.  But resistance is possibly ‘Medium’ under the extreme scenario, so that resilience is ‘Very low’ and sensitivity assessed as ‘Medium’, albeit with ‘Low’ confidence.

Sea-level rise is occurring through a combination of thermal expansion and ice melt.  Sea levels have risen 1-3 mm/yr in the last century (Cazenave & Nerem, 2004, Church et al., 2004, Church & White, 2006). The most recent projections on sea-level rise suggest a rise of 50 cm under the middle emission scenario, 70 cm under the high emission scenario, and 107 cm under the extreme scenario. Species from the genus Bathyporeia and Nephtys cirrosa are abundant at on the Dogger Bank, which has a depth range of 15- 36 m (Wieking & Kröncke, 2003), suggesting that, as long as the habitat remains the same (sand), these species will be tolerant of future sea-level rise for all three scenarios. Nephtys cirrosa occurs on clean sand, down to a depth of 45 m (Rainer, 1991), whilst species of Bathyporeia are often abundant at depths <30 m (Künitzer et al., 1992)

Any potential increase in wave exposure in relation to sea-level rise (e.g. Fujii & Raffaelli, 2008) is not expected to impact this biotope, as these species occur on medium to very fine sand in moderately exposed to exposed areas (JNCC, 2019), therefore an increase in exposure is unlikely to change habitat classification.  However, as wave action is reduced with depth, an increase in depth may stabilize the sediment allowing the habitat to transition into IMuSaFfabMag, resulting in loss of the deeper portions of the biotope. However, over time the biotope may extend inshore, depending on location. Sensitivity assessment. There is likely to be considerable variation between sites, and the depth range occupied by the biotope.  Hence, it is difficult to assess the effect of the different sea-level rise scenarios.  As the biotope can occur from 0-10 m in depth, it is assumed that a sea-level rise of 50 cm, or 70 cm (middle to high emission scenarios) would have limited effect but that a 107 cm rise (the extreme scenario) might result in loss of part of the deeper extent of the biotope in some sites.  Therefore, resistance is assessed as ‘High’ under the middle and high emission scenarios so that resilience is ‘High’ and sensitivity assessed as ‘Not sensitive’.  But resistance is possibly ‘Medium’ under the extreme scenario, so that resilience is ‘Very low’ and sensitivity assessed as ‘Medium’, albeit with ‘Low’ confidence.

Sea-level rise is occurring through a combination of thermal expansion and ice melt.  Sea levels have risen 1-3 mm/yr in the last century (Cazenave & Nerem, 2004, Church et al., 2004, Church & White, 2006). The most recent projections on sea-level rise suggest a rise of 50 cm under the middle emission scenario, 70 cm under the high emission scenario, and 107 cm under the extreme scenario. Species from the genus Bathyporeia and Nephtys cirrosa are abundant at on the Dogger Bank, which has a depth range of 15- 36 m (Wieking & Kröncke, 2003), suggesting that, as long as the habitat remains the same (sand), these species will be tolerant of future sea-level rise for all three scenarios. Nephtys cirrosa occurs on clean sand, down to a depth of 45 m (Rainer, 1991), whilst species of Bathyporeia are often abundant at depths <30 m (Künitzer et al., 1992)

Any potential increase in wave exposure in relation to sea-level rise (e.g. Fujii & Raffaelli, 2008) is not expected to impact this biotope, as these species occur on medium to very fine sand in moderately exposed to exposed areas (JNCC, 2019), therefore an increase in exposure is unlikely to change habitat classification.  However, as wave action is reduced with depth, an increase in depth may stabilize the sediment allowing the habitat to transition into IMuSaFfabMag, resulting in loss of the deeper portions of the biotope. However, over time the biotope may extend inshore, depending on location. Sensitivity assessment. There is likely to be considerable variation between sites, and the depth range occupied by the biotope.  Hence, it is difficult to assess the effect of the different sea-level rise scenarios.  As the biotope can occur from 0-10 m in depth, it is assumed that a sea-level rise of 50 cm, or 70 cm (middle to high emission scenarios) would have limited effect but that a 107 cm rise (the extreme scenario) might result in loss of part of the deeper extent of the biotope in some sites.  Therefore, resistance is assessed as ‘High’ under the middle and high emission scenarios so that resilience is ‘High’ and sensitivity assessed as ‘Not sensitive’.  But resistance is possibly ‘Medium’ under the extreme scenario, so that resilience is ‘Very low’ and sensitivity assessed as ‘Medium’, albeit with ‘Low’ confidence.

The amphipods that occur within this habitat are mobile and can avoid unfavourable conditions to some extent. Bathyporeia life cycles vary between locations and this is related to temperature (Mettam, 1989). Preece (1971) tested temperature tolerances of Bathyporeia pelagica and Bathyporeia pilosa in the laboratory.  Individuals acclimated to 15^oC for 24 hours were exposed to temperature increases (water temperature raised by 0.2^oC/minute). As test  temperature were reached individuals were removed, placed in seawater at 4^oC and allowed to recover for 24 hours at which point mortalities were tested. Amphipods were also allowed to bury into sediments and held at test temperatures for 24 hours of 32.5^oC, 31.8^oC and 29.5^oC before being allowed to recover in fresh seawater at 15^oC for a further 24 hours, before mortalities were assessed. Upper lethal temperatures (the temperature at which 50% of individuals died for adult males and gravid females of Bathyporeia pilosa were 37.5^oC and 39.4^oC, respectively. Bathyporeia pelagica exhibited lower tolerances and adult males and gravid females had upper lethal temperature tolerances of 33.4 and 34.2^oC respectively. These tests measures short-term exposure only and species had lower tolerance for longer-term (24 hour exposure).  No mortality occurred for Bathyporeia pilosa individuals held at 29.5^oC and 30.8^oC; however 15% of individuals exposed to water temperatures of 31.8^oC and 96% at 32.5^oC died. Bathyporeia pelagica exhibited lower tolerances, 11% of individuals died after 24 hr exposure to 29.5^oC and 100% mortality occurred at 30.8^oC and above (Preece, 1971).

Emery et al. (1957) reported that Nephtys spp. could withstand summer temperatures of 30-35°C so is likely to withstand the benchmark acute temperature increase. An acute increase in temperature at the benchmark level may result in physiological stress endured by the infaunal species but is unlikely to lead to mortality.

Sensitivity assessment. Typical surface water temperatures around the UK coast vary seasonally from 4-19 ^oC (Huthnance, 2010).  A chronic increase in temperature throughout the year of 2^oC may fall within the normal temperature variation and an acute increase in water temperatures from 19 to 24^oC for a month may be tolerated by the characterizing species supported by deeper burrowing and/or migration. For Bathyporeia spp. temperature increases above 30^oC appear to be critical based on Preece (1971). Biotope resistance is therefore assessed as ‘High’ and resilience as ‘High’ so that the biotope is assessed as ‘Not sensitive’. Increased water and air temperatures and desiccation may lead to greater synergistic effects and the loss of characterizing amphipods and isopods may result in shifts between the variant sub-biotopes. 

Crisp (1964) reported that species of amphipod and isopods seemed to be unharmed by the severe winter of 1962-1963. This may be due to burial in sediments buffering temperature or seasonal migration to deeper waters to avoid freezing. 

Preece (1971) tested the temperature tolerances of Bathyporeia pelagica and Bathyporeia pilosa in the laboratory.  Individuals acclimated to 15^oC for 24 hours were placed in a freezer in wet sediment. As test temperatures were reached individuals were removed and allowed to recover for 24 hours at which point mortalities were tested. Amphipods were also allowed to bury into sediments and held at test temperatures of -1^oc, -3^oC and -5^oC for 24 hours before being allowed to recover in fresh seawater at 15^oC for a further 24 hours before mortalities were assessed. Lower lethal short-term tolerances of Bathyporeia pilosa and Bathyporeia pelagica were -13.6^oC and -6.4^oC respectively.  Sensitivity to longer-term exposure is greater, especially for Bathyporeia pelagica. Bathyporeia pilosa individuals could withstand temperatures as low as -1^oC for 24 hours, while 42% of Bathyporeia pelagica died. At -3^oC 5% of Bathyporeia pilosa died (100% of Bathyporeia pelagica) but this rose to 82% at -5^oC.

Nephtys cirrosa reaches its northern limit in Scotland, and German Bight of the North Sea. A decrease in temperature is likely to result in loss of the species from the SS.SSa.SSaVS biotope in Scotland.

Sensitivity assessment. Typical surface water temperatures around the UK coast vary seasonally from 4-19 ^oC (Huthnance, 2010).  A chronic decrease in temperature throughout the year of 2^oC may fall within the normal temperature variation but an acute decrease in water temperatures from 4^oC to -1^oC at the coldest part of the year may lead to freezing and lethal effects on for a month may be tolerated by the characterizing species supported by deeper burrowing and/or migration to deeper waters. For Bathyporeia spp. seawater temperature decreases below -1^oC appear to be critical based on Preece (1971). Biotope resistance is therefore assessed as ‘Medium’ and resilience as ‘High’ so that biotope sensitivity is assessed as 'Low'.

This biotope is found in full salinity (30-35 ppt) habitats (JNCC, 2015), a change at the pressure benchmark is therefore assessed as a change to hypersaline conditions. Little evidence was found to assess responses to hypersalinity. However, monitoring at a Spanish desalination facility where discharges close to the outfall reached a salinity of 53, found that amphipods were sensitive to the increased salinity and that species free-living in the sediment were most sensitive. The study area did not host any of the species characterizing this biotope but the results indicate a general sensitivity (De-la-Ossa-Carretero, et al., 2016).

Sensitivity assessment.  Not assessed, ‘No evidence’.

The biotope is found in full salinity habitats (JNCC, 2015). A change at the pressure benchmark refers to a decrease from full to variable (18-35 ppt), or to reduced salinity (18-30 ppt). Bathyporeia pelagica migrates seaward in response to reduced salinities, the effect of which is enhanced by higher temperature (Preece, 1970). Bathyporeia pilosa is, however, more tolerant of low salinities and is capable of reproducing at salinities as low as 2 (Khayrallah, 1977). Populations of Bathyporeia pilosa within the upper reaches of the Severn Estuary experience wide fluctuations in salinity ranging from 1-22 depending on the season and tidal cycle (Mettam, 1989). The physiological stress for this environment affects size and reproduction (Mettam, 1989). Speybroeck et al. (2008) noted that Bathyporeia pilosa tends to occur subtidally in estuarine and brackish conditions. Local populations may be acclimated to the prevailing salinity regime and may exhibit different tolerances to other populations subject to different salinity conditions and, therefore, caution should be used when inferring tolerances from populations in different regions.  

A reduction in salinity at the pressure benchmark could result in the loss of species or changes in abundance and biotope reversion to the biotope SS.SSa.SSaVS.MoSaVS which occurs in typical mobile sand conditions but in reduced salinities and lacks Nepthys cirrosa and Bathyporeia spp. (although these may be washed in from adjacent communities) (JNCC, 2015) or a change to SS.SSa.SSaVS.NcirLim, which occurs in variable salinity and contains the bivalve  Macoma balthica.

Sensitivity assessment. A decrease in salinity is likely to lead to changes in species abundance and richness and may lead to biotope reclassification. Biotope resistance is assessed as ‘None’ and resilience as ‘High’ (following restoration of typical habitat conditions). Sensitivity is therefore assessed as ‘Medium’. 

Water movement is a key factor physically structuring this biotope although exposure to wave action may be more significant for many examples than tidal streams. This biotope is recorded where tidal streams are weak (<0.5 m/s)or very weak (negligible) (JNCC, 2015), in areas where flows are lower, wave action may be more important in maintaining the sediment mobility that structures the biotope.  Where similar sand habitats occur in  more sheltered areas the biological structure alters in response to the increased or decreased sediment mobility with Magelona mirabilis found in higher abundances in more sheltered habitats and Chaetozone setosa found in more disturbed habitats (JNCC, 2015). An increase in disturbance may lead to biotope reversion to the similar biotope SS.SSa.IFiSa.IMoSa which occurs in more disturbed areas. A decrease in disturbance may lead to changes to SS.SSa.IMuSa.FfabMag, where finer sediments are deposited.

Sensitivity assessment. The sediments that characterize this biotope and sub-biotopes are mobile sands that range from medium to fine, a change at the pressure benchmark (increase or decrease) may lead to some changes in sediment sorting. Based on the range of water flows experienced, biotopes occurring in habitats at the middle of the range are considered to be 'Not sensitive' to an increase or decrease in flow at the pressure benchmark. Changes in water flow in areas sheltered from wave action could. however, lead to changes in biotope classification due to the increase in sediment stability.

Not relevant to sublittoral biotopes.​

Water movement is a key factor physically structuring this biotope, with sediment sorting and mobilisation by tidal streams and wave action modifying the sediments present and the level of disturbance. The assessed biotope is found in habitats that are exposed to sheltered from wave action (JNCC, 2015).

Sensitivity assessment. Wave action is a key factor structuring this biotope through sediment mobility.  As the biotope occurs across two wave exposure categories (JNCC, 2015) this is considered to indicate, by proxy, that a change in wave exposure at the pressure benchmark is less than the natural range of wave heights experienced.  Biotope resistance to this pressure is therefore assessed as ‘High’ and resilience as ‘High (by default) so that the biotope is considered to be ‘Not sensitive’ at the pressure benchmark. 

This pressure is Not assessed but evidence is presented where available.

Levels of contaminants that exceed the pressure benchmark may cause impacts. For most metals, toxicity to crustaceans increases with decreased salinity and elevated temperature, therefore marine species living within their normal salinity range may be less susceptible to heavy metal pollution than those living in salinities near the lower limit of their salinity tolerance (McLusky et al., 1986). Jones (1973; 1975b) found that mercury (Hg) and copper (Cu) reacted synergistically with changes in salinity and increased temperature (10°C) to become increasingly toxic to species of isopod, including Eurydice pulchra.

This pressure is Not assessed but evidence is presented where available.

This pressure is Not assessed but evidence is presented where available.

In general, crustaceans are widely reported to be intolerant of synthetic chemicals (Cole et al., 1999) and intolerance to some specific chemicals has been observed in amphipods. Powell (1979) inferred from the known susceptibility of Crustacea to synthetic chemicals and other non-lethal effects, that there would probably also be a deleterious effect on isopod fauna as a direct result of chemical application. All were killed at about 10 ppm BP 1002 after 24 hours exposure, whilst at 5 ppm four out of five individuals survived when transferred to clean seawater.

No evidence.

This pressure is Not assessed.

Information concerning the reduced oxygen tolerance of Nephtys cirrosa was not found but evidence (Alheit, 1978; Arndt & Schiedek, 1997; Fallesen & Jørgensen, 1991) indicated a similar species, Nephtys hombergii, to be very tolerant of episodic oxygen deficiency and at the benchmark duration of one week.

Laboratory studies by Khayrallah (1977) on Bathyporeia pilosa, indicated that it has a relatively poor resistance to conditions of hypoxia in comparison to other interstitial animals. However, Mettam (1989) and Sandberg (1997) suggest that Bathyporeia pilosa can survive short-term hypoxia.

Sensitivity assessment.  This biotope  is characterized by mobile sands in areas that experience strong water flows or are wave exposed. The mixing effect of wave action and water movement will limit the intensity and duration of exposure to deoxygenated waters. The species characterizing the biotope are also mobile and able to migrate vertically or shorewards to escape unsuitable conditions. Biotope resistance is therefore assessed as ‘High’ and resilience as ‘High’ (by default) so that the biotope is considered to be ‘Not sensitive’.

In-situ primary production is limited to microphytobenthos within and on sediments and the high levels of sediment mobility may limit the level of primary production as abrasion would be likely to damage diatoms (Delgado et al., 1991). The amphipods feed on epipsammic diatoms attached to the sand grains (Nicolaisen & Kanneworff, 1969). Both these groups may benefit from slight nutrient enrichment if this enhanced primary production. 

Sensitivity assessment.  Nutrient level is not a key factor structuring the biotope at the pressure benchmark. In general, however, primary production is low and this biotope is species poor and characterizing species may be present at low abundances (depending on sediment mobility). Biotope resistance is therefore assessed as ‘High’, resilience as ‘High’ (by default) and the biotope is considered to be ‘Not sensitive’.

The biotope occurs in mobile sand sediments where wave action leads to particle sorting, in-situ primary production is restricted to microphytobenthos although sediment mobility may restrict production levels (Delgado et al., 1991). 

Sensitivity assessment.  At the pressure benchmark organic inputs are unlikely to significantly affect the structure of the biological assemblage or impact the physical habitat, due to remobilisation and transport by wave or currents. Biotope sensitivity is therefore assessed as ‘High’ and resilience as ‘High’ (by default) and the biotope is therefore considered to be ‘Not sensitive’.

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.

The biotope is characterized by the sedimentary habitat (JNCC, 2015), a change to an artificial or rock substratum would alter the character of the biotope leading to reclassification and the loss of the sedimentary community including the characterizing polychaetes and amphipods.

Sensitivity assessment. Based on the loss of the biotope, resistance is assessed as ‘None’, recovery is assessed as ‘Very low’ (as the change at the pressure benchmark is permanent and sensitivity is assessed as ‘High’.

The pressure benchmark refers to the simplified Folk classification developed by Long (2006) and the UK Marine Habitat Classification Littoral and Sublittoral Sediment Matrices (Connor et al., 2004). The biotope occurs on mobile sands, a change at the pressure benchmark refers to a change to sandy muds or muddy sands or to coarser gravel sediments. Experiments by Van Tomme et al. (2013) have shown that the optimal sedimentary habitats for some of he species that characterize this biotope vary slightly. Bathyporeia pilosa prefer the finest sediments, although at a subtidal dredge disposal site the change to a finer sediment led to a reduction in the abundance of Bathyporeia pilosa (Witt et al., 2004). Bathyporeia sarsi has a broader preference and also occurred in medium-coarse sediments (Van Tomme et al., 2013). 

Nepthys cirrosa occurs in fine to coarser sands, with greatest abundance in the Belgium part of the North Sea recorded in medium grain sizes (Degraer et al., 2006). A change to gravelly sand is unlikely to impact this species, however, a change to muddy sand may limit the species abundance as the species displays a slight preference for low mud content levels (< 10%) (Degraer et al., 2006).  

Sensitivity assessment. A change to either a finer muddy sediment or a coarser sediment, is likely to lead to changes in the abundance and identity of the characterizing species . Based on the loss of the biotope, resistance is assessed as ‘None’, recovery is assessed as ‘Very low’ (as the change at the pressure benchmark is permanent and sensitivity is assessed as ‘High’.

Bathyporeia pelagica lives infaunally in the uppermost 3 cm of sandy substrata as does the isopod Eurydice pulchra (Fish, 1970). Extraction of the sediment to 30cm is likely to remove the characterizing polychaetes, amphipods and isopods within the footprint (although if disturbed some may be able to escape). 

Sensitivity assessment. Biotope resistance to extraction of sediment and characterizing species is assessed as ‘None. Resilience is assessed as ‘High’, as sediment recovery will be enhanced by wave action and mobility of sand. The characterizing species are likely to recover through transport of adults in the water column or migration from adjacent patches. Biotope sensitivity is therefore assessed as ‘Medium’.

This biotope group is present in mobile sands, the associated species are generally present in low abundances and adapted to frequent disturbance suggesting that resistance to surface abrasion would be high. The amphipod and isopod species present are agile swimmers and are characterized by their ability to withstand sediment disturbance (Elliott et al. 1998). Similarly, the polychaete Nephtys cirrosa is adapted to life in unstable sediments and lives within the sediment. This characteristic is likely to protect this species from surface abrasion.

Comparisons between shores with low and high levels of trampling found that the amphipod Bathyporeia pelagica is sensitive to abrasion and compaction from human trampling, other species including Pontocrates arenarius and the isopod Eurydice affinis also decreased in response to trampling but Bathyporeia pelagica appeared to be the most sensitive  (Reyes-Martínez et al., 2015).  

Sensitivity assessment. Resistance to a single abrasion event is assessed as ‘Low’ based on the evidence for trampling from Reyes-Martínez et al. (2015). Resilience is assessed as ‘High’, based on migration from adjacent populations and in-situ reproduction by surviving amphipods.  Sensitivity is therefore assessed as ‘Low’. This assessment may underestimate sensitivity to high-levels of abrasion (repeated events within a short period). The trampling evidence and the evidence for penetration from mobile gears (see below) differ in the severity (resistance) of impact. This may be due to different levels of intensity (multiple trampling/abrasion events vs single penetration/towed gear impacts) or the nature of the pressure. Abrasion from trampling also involves a level of compaction that could collapse burrows and damage species through compression. Penetration may, however, break sediments open allowing mobile species to escape or species may be pushed forwards from towed gear by a pressure wave where this is deployed subtidally (Gilkinson et al., 1998). Both risk assessments are considered applicable to single events based on the evidence and the sensitivity assessment for both pressures is the same although resistance differs. 

This biotope group is present in mobile sands, the associated species are generally present in low abundances and adapted to frequent disturbance suggesting that resistance to abrasion and penetration and disturbance of the sediment would be high. The amphipod  species present are agile swimmers and are characterized by their ability to withstand sediment disturbance (Elliott et al., 1998).

Bergman and Santbrink (2000) found that direct mortality of gammarid amphipods, following a single passage of a beam trawl (in silty sediments where penetration is greater) was 28%. Similar results were reported from experiments in shallow, wave disturbed areas, using a toothed, clam dredge. Bathyporeia spp. experienced a reduction of 25% abundance in samples immediately after intense clam dredging, abundance recovered after 1 day (Constantino et al. 2009). Experimental hydraulic dredging for razor clams resulted in  no statistically significant differences in Bathyporeia elegans abundances between treatments after 1 or 40 days (Hall et al., 1990), suggesting that recovery from effects was very rapid. Ferns et al. (2000) examined the effects of a tractor-towed cockle harvester on benthic invertebrates and predators in intertidal plots of muddy and clean sand. Harvesting resulted in the loss of a significant proportion of the most common invertebrates from both areas. In the muddy sand, the population of Bathyporeia pilosa remained significantly depleted for more than 50 days, whilst the population in clean sand recovered more quickly. These results agree with other experimental studies that clean sands tend to recover more quickly that other habitat types with higher proportions of fine sediment (Dernie et al., 2003).

Sensitivity assessment. Based on the evidence above it is considered that Bathyporeia spp. and other characterizing species will have ‘Medium’ resistance (mortality <25%) to abrasion, their small size, infaunal position and mobility enabling a large proportion of the population to escape injury. Recovery is assessed as ‘High’ and sensitivity is therefore categorised as ‘Low’.The trampling evidence (see above) and the evidence for penetration from mobile gears  differ in the severity (resistance) of impact. This may be due to different levels of intensity (multiple trampling/abrasion events vs single penetration/towed gear impacts) or the nature of the pressure. Abrasion from trampling also involves a level of compaction that could collapse burrows and damage species through compression. Penetration may, however, break sediments open allowing mobile species to escape or species may be pushed forwards from towed gear by a pressure wave where this is deployed subtidally (Gilkinson et al., 1998). 

The characterizing species live within the sand and are unlikely to be directly affected by an increased concentration of suspended matter in the water column. Within the mobile sands habitat storm events or spring tides may re-suspend or transport large amounts of material and therefore species are considered to be adapted to varying levels of suspended solids.

 Bathyporeia spp. feed on diatoms within the sand grains (Nicolaisen & Kanneworff, 1969), an increase in suspended solids that reduced light penetration could alter food supply. However, diatoms are able to photosynthesise while the tide is out and therefore a reduction in light during tidal inundation may not affect this food source , depending on the timing of the tidal cycle.

Amphipods may be regular swimmers within the surf plankton, where the concentration of suspended particles would be expected to be higher (Fincham, 1970a). Furthermore, during the winter, when Bathyporeia pelagica extends its distribution into the mouths of estuaries the species may encounter concentrations of suspended sediment measurable in grams per litre (benchmark is mg/l) (Cole et al. 1999).  

Sensitivity assessment. Increased inorganic suspended solids may increase abrasion but it is likely that the infaunal species would be unaffected. The biotope is considered to be ‘Not sensitive’ to a decrease in suspended solids that does not affect sediment transport and supply to the biotope. Biotope resistance is assessed as ‘Medium’ as some effects on feeding and diatom productivity may occur from increases in suspended solids, resilience is assessed as ‘High’, following a return to usual conditions and sensitivity is assessed as ‘Low’. This more precautionary assessment is presented in the table.  Indirect effects such as deposition, erosion and associated sediment change that may result from changes in suspended solids in the long-term are assessed separately. 

Evidence for the effects of siltation by thick layers of added sediment from beach nourishment is described for the heavy deposition pressure below. The pressure benchmark for light deposition refers to the addition of a relatively thin layer of deposits in a single event.  Species adapted to coarse sediments may not be able to burrow through fine sediments, or experienced reduced burrowing ability. For example, Bijkerk (1988, results cited from Essink, 1999) found that the maximal overburden through which Bathyporeia could migrate was approximately 20 cm in mud and 40 cm in sand.  No further information was available on the rates of survivorship or the time taken to reach the surface.

Sensitivity assessment.  As the biotope is associated with wave exposed habitats or those with strong currents, some sediment removal will occur, mitigating the effect of deposition. The mobile polychaete Nephtys cirrosa and amphipods are likely to be able to burrow through a 5cm layer of fine sediments. Biotope resistance is therefore assessed as ‘High’ and resilience as ‘High’ (by default). The biotope is therefore considered to be ‘Not sensitive’ to this pressure.  Repeated deposits or deposits over a large area or in sheltered systems that were shifted by wave and tidal action may result in sediment change (see physical change pressure).

Studies have found that beach ‘replenishment’ or ‘nourishment’ that involves the addition of sediments on beaches can have a number of impacts on the infauna (Peterson et al., 2000, Peterson et al., 2006). Impacts are more severe when the sediment added differs significantly in grain size or organic content (Nelson et al., 1989, Peterson et al., 2000).  For example, Maurer et al. (1981) found that the amphipod Parahaustorius longimerus which occurs intertidally in clean, well-sorted sands and is an active, effective burrower was able to regain the surface after being buried by sand far more easily than when buried under silt/clay mixtures.

A thick layer of sediment has a smothering effect and in most instances buried species will die although some polychaetes can escape up to 90cm of burial In response to nourishment (Speybroek et al., 2007, references therein). Peterson et al. (2000) found that the dominant macrofauna were reduced by 86-99% 5-10 weeks after the addition of sediment that was finer than the original sediments but with a high shell content.

Little empirical information was found for the ability of characterizing species to reach the surface after burial. Bijkerk (1988, results cited from Essink, 1999) found that the maximal overburden through which Bathyporeia could migrate was approximately 20 cm in mud and 40 cm in sand.  No further information was available on the rates of survivorship or the time taken to reach the surface and no information was available for other characterizing species.

Leewis et al. (2012) investigated the recovery of  Bathyporeia sarsi, following beach nourishment by comparing beaches that had been exposed at different times. The lengths of beach nourished varied from 0.5 kn to > 7 km.  Recovery to original abundances appeared to occur within one year for the characterizing species which were in agreement with other studies (Leewis et al., 2012 and references therein).  

Repeated events are not considered at the pressure benchmark but it is noted that annual beach nourishment can alter beach sediments (see physical change pressure) and result in suppression of macroinvertebrate populations (Manning et al., 2014).

Sensitivity assessment. The thickness of sediment applied during beach nourishment is likely to exceed the 30cm pressure benchmark but the results from studies on the activity are informative, particularly with regard to recovery rate. Sediment removal by wave action could mitigate the level of effect but overall smothering by fine sediments is likely to result in mortality of characterizing amphipods and isopods and possibly Nephtys cirrosa. Biotope resistance is therefore assessed as ‘Low’ and resilience as High (based on Leewis et al., 2012), biotope sensitivity is therefore assessed as ‘Low’.

This pressure is not assessed. Amphipods may also consume microplastics although no negative effects have been documented. Ugolini et al. ( 2013) found that Talitrus saltator could consume polyethylene microspheres.  Most microspheres were expelled in 24 h. and were totally expelled in one week. microsphere ingestion on the survival capacity in the laboratory. Analyses carried out on faeces of freshly collected individuals revealed the presence of polyethylene and polypropylene, confirming that microplastic debris could be swallowed by Talitrus saltator in natural conditions. The talitrid Orchestia gammarellus has also been recorded as ingesting microplastics in the size range 20-200µm (Thompson et al., 2004).

No evidence for the characterizing species was found to assess this pressure. For some amphipods there is evidence for geomagnetic orientation being inhibited or disrupted by the presence of electromagnetic fields or by changing magnetic fields. Arendse & Barendregt (1981) manipulated magnetic fields to alter orientation of the talitrid amphipod Orchestia cavimana. 

Deep-water amphipods Gondogenia arctica have been shown to be sensitive to even weak electromagnetic fields which cancel magnetic orientation (Tomanova & Vacha, 2016). Loss of orientation was observed at a radiofrequency electromagnetic field of 2 nT (0.002  µT) (Tomanova & Vacha, 2016).

Not relevant.

As this feature is not characterized by the presence of primary producers it is not considered that shading would alter the character of the habitat. No specific evidence was found to assess the sensitivity of the characterizing species to this pressure. Changes in light level may, however, affect activity rhythms of the invertebrates. Amphipods within the biotope prefer shade and therefore an increase in light may inhibit activity, particularly at night when they emerge from the sediment and are most active (Jelassi et al., 2015; Ayari, 2015). Hartwick (1976) found that artificial lighting interfered with learning or orientation cues by Talitrids.  

Orientation by light has been well studied for intertidal amphipods (particularly Talitrus saltator). Intertidal amphipods orientate themselves by a range of factors that include (but are not limited to) visual cues based on solar or astronomic cues such as the moon and the geomagnetic field (Scapini, 2014). Activity patterns are also linked to internal biological clocks that respond to diel, tidal, lunar and seasonal cycles, so that animals are active during the most suitable time of day or night (Scapini, 2014).  The introduction of light or an increase in shading could, therefore, alter behavioural patterns and navigation.

Changes in light and level of shade may indirectly affect the characterizing Bathyporeia spp. through changes in  behaviour and food supply via photosynthesis of diatoms within sediments. Benthic microalgae play a significant role in system productivity and trophic dynamics, as well as habitat characteristics such as sediment stability (Tait & Dipper, 1998). Shading could prevent photosynthesis leading to death or migration of sediment diatoms altering sediment cohesion and food supply to the grazing amphipods.

Sensitivity assessment. Changes in light are not considered to directly affect the biotope however, some changes in behaviour or food supply for Bathyporeia spp could result. Sensitivity is assessed as ‘Medium’ and resilience is assessed as ’High’. Biotope sensitivity is, therefore, assessed as ‘Low’.

As the amphipods and isopods that characterize this biotope have benthic dispersal strategies (via brooding), water transport is not a key method of dispersal over wide distances, as it is for some marine invertebrates that produce pelagic larvae such as the characterizing Nephtys cirrosa.  Barriers that limit tidal excursion and flushing may reduce connectivity or help to retain larvae.

Sensitivity assessment. The biotope (based on the biological assemblage) is considered to have ‘High’ resistance to the presence of barriers that lead to a reduction in tidal excursion, resilience is assessed as ‘High’ (by default) and the biotope is considered to be ‘Not sensitive’.

Not relevant’ to seabed habitats.  NB. Collision by grounding vessels is addressed under ‘surface abrasion.

The characterizing species are likely to be able to detect light and some movement but are unlikely to have any visual acuity and are considered to not be sensitive to this factor. The amphipods emerge from the sediments at night and are unlikely to be disturbed although like many species they may flee from movements.

Key characterizing species within this biotope are not cultivated or translocated. This pressure is therefore considered ‘Not relevant’ to this biotope group.

The North American amphipod Gammarus tigrinus was detected in the north-eastern Baltic Sea in 2003 and has rapidly expanded into European waters since (Jänes et al., 2015).  Native gammarids, such as Gammarus salinus have almost disappeared from some habitats of the northeastern Baltic Sea and the competition for space between the invasive Gammarus tigrinus the native Gammarus salinus has been a contributing factor in certain habitats (Kotta et al., 2011). Competition for space alone did not explain the mass disappearance of Gammarus salinus as Gammarus tigrinus did not out-compete Gammarus salinus in all Baltic Sea habitats, limiting confidence in the evidence. However, Gammarus tigrinus has been identified in many UK estuaries and coasts and appears likely to influence species composition in the biotope (NBN Gateway 2016). This species prefers lower salinities and is typical of brackish waters (Kotta et al., 2013) and is therefore not considered a threat to this biotope where salinities are unaltered from the usual full salinity conditions.

Sensitivity assessment. The sediments characterizing this biotope are mobile and frequent disturbance limits the establishment of marine and coastal invasive non-indigenous species as the habitat conditions are unsuitable for most species, as exemplified by the low species richness characterizing this biotope.This biotope is therefore considered to have 'High' resistance to this pressure and high resilience (by default), and is assessed as 'Not sensitive' to this pressure.

 Amphipods may also be infected by a number of parasites or pathogens that alter population numbers through changes in host condition, growth, behaviour and reproduction (Green Extabe & Ford, 2014). Infection by acanthocephalan larvae, for example, may alter behaviour and responses of gammarid amphipods (Bethel & Holmes, 1977). 

No evidence was found for pathogen/parasite outbreaks that may result in mass-mortalities in the characterizing species and this pressure is not assessed.

Intertidal populations of Nepthys cirrosa may be targeted by bait diggers.  There is limited information on the effect of digging directly on Nephtys cirrosa populations, however there is evidence on effects on another Nephtys species: Nephtys hombergii. Nephtys hombergii is directly removed through commercial bait digging and by recreational anglers and abundance significantly decreased in areas of the Solent, UK, where bait digging (primarily for Nereis virens) had occurred (Watson et al. 2007). Recovery of Nephtys hombergii has been assessed to be very high as re-population would occur initially relatively rapidly via adult migration and later by larval recruitment. Dittman et al. (1999) observed that Nephtys hombergii was amongst the macrofauna that colonized experimentally disturbed tidal flats within two weeks of the disturbance that caused defaunation of the sediment. However, if sediment is damaged recovery is likely to be slower, for instance Nephtys hombergii abundance was reduced by 50% in areas where tractor towed cockle harvesting was undertaken on experimental plots in Burry inlet, south Wales, and had not recovered after 86 days (Ferns et al., 2000).

Sensitivity assessment. Although Nephtys cirrosa may be targeted by bait differs where this species occurs intertidally, subtidal populations are not considered to be impacted unless there was a change in emergence regime. This pressure is, therefore considered to be 'Not relevant' to the assessed biotope.

The loss of the key characterizing species through unintentional removal would alter the character of the biotope. The ecosystem services such as secondary production and food for higher trophic levels would be lost. The polychaete Nephtys cirrosa and the amphipods are predated on by flat fish and other invertebrate predators during tidal inundation (Speybroeck et al., 2007; Van Tomme et al., 2014).

Sensitivity assessment. Biotope resistance to loss of the characterizing species is assessed as ‘Low’ as the burrowing lifestyle and mobility of species mean that a proportion of the population may escape incidental removal. Resilience is assessed as ‘High’ based on in-situ recovery and migration from adjacent populations and sensitivity is therefore assessed as ‘Low’. Despite the loss of a high proportion of the characterizing species  the biotope would still be classified as belonging to the LS.LSa.MoSa group as some examples, particularly those that are very exposed to wave action, contain few species at low abundance (JNCC, 2015).