MarLIN

information on the biology of species and the ecology of habitats found around the coasts and seas of the British Isles

Capitella capitata in enriched sublittoral muddy sediments

23-06-2009
Researched byDr Heidi Tillin Refereed byAdmin
EUNIS CodeA5.336 EUNIS NameCapitella capitata in enriched sublittoral muddy sediments

Summary

UK and Ireland classification

EUNIS 2008A5.336Capitella capitata in enriched sublittoral muddy sediments
EUNIS 2006A5.336Capitella capitata in enriched sublittoral muddy sediments
JNCC 2004SS.SMu.ISaMu.CapCapitella capitata in enriched sublittoral muddy sediments
1997 BiotopeSS.IMS.FaMS.CapCapitella capitata in enriched sublittoral muddy sediments

Description

The polychaete Capitella capitata (agg.) a widely-occurring, opportunist species complex that is particularly associated with organically enriched and polluted sediments (Warren, 1977; Pearson & Rosenberg,1978) where it may be superabundant. In very polluted/disturbed areas only Capitella, nematodes and occasional Malacoceros fuliginosus may be found whilst in slightly less enriched areas and estuaries species such as Tubificoides, Cirriformia tentaculata, Pygospio elegans and Polydora ciliata may also be found. In some areas e.g. the Tees Estuary, high numbers of the polychaete Ophryotrocha may also be present. Cap may become established as a result of anthropogenic activities such as fish farming and sewerage effluent but may also occur with natural enrichment as a result of, for example, coastal bird roosts. This biotope may also occur to some extent in the intertidal and in estuaries (JNCC, 2015).

Recorded distribution in Britain and Ireland

-

Depth range

0-5 m, 10-20 m, 5-10 m

Additional information

None entered.

Listed By

Further information sources

Search on:

JNCC

Habitat review

Ecology

Ecological and functional relationships

  • Capitella capitata represents a complex (Grassle & Grassle, 1976) of over ten sibling species (Gemenick & Giere, 1997) which are likely to be present in the biotope. While the species of this complex show only slight differences in adult morphology, they differ widely in ontogenetic, ecological and genetic features (Gamenick & Giere, 1997) and have distinct reproductive modes (Grassle & Grassle, 1976).
  • Capitella capitata has been recorded in high numbers in areas of organic enrichment, where sewage inputs (Bridges, 1996; Holte & Oug, 1996; Cardell et al., 1998, Thom & Chew, 1979) and fish farms (Karakassis et al., 2000) were present. It has also been recorded in areas where sediments contain high concentrations of metals and hydrocarbons (Ward & Young, 1982; Olsgard, 1999; Petrich & Reish, 1979). The species is commonly cited as an indicator of organic enrichment, although members of the species complex vary in their response to disturbance and environmental change.
  • The conditions in which Capitella capitata flourishes are not tolerated by many other organisms. Thus, when members of the species complex occur in high densities few other species will be present.
  • Capitella capitata is also found in organically poor areas (Eagle & Rees, 1973) although it is unlikely to be present in such high abundance in these habitats because of competition from other species. Capitella capitata is a complex of opportunistic species with life history traits that enable them to rapidly colonize vacant and disturbed habitats. Thus, in areas of high disturbance, by regular dredging for instance, Capitella capitata may be present.
  • Lugworms have been found to have a strongly negative effect on the juvenile densities of Capitella capitata (Flach, 1991).

Seasonal and longer term change

  • Although annual variations in the composition of cryptic species within the Capitella capitata complex have been documented (Grassle & Grassle, 1976), very little information has been found on seasonal or temporal changes in overall Capitella capitata populations.
  • Differences, sometimes distinctly seasonal, may be observed in the breeding period of Capitella capitata according to variation in local conditions, especially temperature, organic enrichment of the sediment and population density. For example, Mendez et al. (1997) suggest that Capitella capitata is able to produce many individuals when organic supply is high enough to feed all the population. However, variation in reproductive output is also likely to be determined by differences in composition of the Capitella capitata species complex, as members are known to differ in fecundity, larval dispersal ability and general abundance (Grassle & Grassle, 1978).
  • In the sheltered conditions in which the biotope is found it, is unlikely that winter weather disturbance is likely to have an impact on population demographics.

Habitat structure and complexity

  • The biotope has very little structural complexity with Capitella capitata, and the few other species that may be present, living in or on the sediment.
  • Deposit feeders manipulate, sort and process sediment particles and may result in destabilization and bioturbation of the sediment which inhibits survival of suspension feeders.

Productivity

Productivity in IMS.Cap is mostly secondary, derived from detritus and organic material. Macroalgae are absent from the biotope. The biotope occurs in nutrient rich areas, for example, close to sewage outfalls. Allochthonous organic material is derived from anthropogenic activity (e.g. sewerage) and natural sources (e.g. plankton, detritus). Autochthonous organic material is formed by benthic microalgae (microphytobenthos e.g. diatoms and euglenoids) and heterotrophic micro-organism production. Organic material is degraded by micro-organisms and the nutrients are recycled. Productivity in the biotope is expected to be high. Many of the characterizing species are likely to have a short life span, grow to maturity quickly and have multiple generations per year. Mendez et al. (1997) suggested that Capitella capitata is able to produce many individuals when organic supply is high enough to feed all the population, although the ability and timescale of response varies among members of the species complex (Grassle & Grassle, 1978).

Recruitment processes

  • Warren (1976) noted that spawning of Capitella capitata occurred throughout the year in Plymouth, with all oocytes being released at a single spawning. Warren (1976) also noted that oocytes are not released into the coelomic fluid until almost fully developed and that larval development may have been completely benthonic. However, in the USA another variant of the Capitella capitata complex, Capitella species 1, has been shown to have planktonic larval development for a short time (hours to days) before settlement (Grassle & Grassle, 1974). Generally speaking, this species is considered to be iteroparous, and the larvae are brooded during part of their development within the adult tube.
  • Planas & Mora (1989) have calculated that individuals from the northwest of Spain spend 2-4 weeks to change from eggs to the juvenile stage and about 3 months from juveniles to adults.
  • Studies on natural populations of Capitella capitata in England show that sexual maturity is reached at about 4 months (Warren, 1976). However, in other geographical locations, sexual maturity may be reached at 3.5 months (Qian & Chia, 1994).
  • Capitella species 1 larvae were attracted by a sulphide concentration of 0.1 mm to 1.0 mm, yielding higher settlement, subsequent metamorphosis and survival of settled polychaetes compared with non-sulphidic controls (Cuomo, 1985).

Time for community to reach maturity

A Capitella capitata biotope is likely to reach maturity very rapidly because the species of the complex are short lived, reaching maturity within about four months. Capitella capitata has an opportunistic life history and year round breeding. Bolam & Fernandes (2002) and Shull (1997) noted that Capitella capitata can colonize azoic sediments rapidly in relatively high numbers. Shull (1997) also demonstrated that this occurs by larval settlement, bedload transport and by burrowing. Thus, when conditions are suitable, the time for the community to reach maturity is likely to be less than six months.

Additional information

None

Preferences & Distribution

Recorded distribution in Britain and Ireland

Habitat preferences

Depth Range 0-5 m, 10-20 m, 5-10 m
Water clarity preferences
Limiting Nutrients Not relevant
Salinity Full (30-40 psu), Low (<18 psu), Variable (18-40 psu)
Physiographic
Biological Zone Infralittoral
Substratum Mud
Tidal Moderately Strong 1 to 3 knots (0.5-1.5 m/sec.), Weak < 1 knot (<0.5 m/sec.)
Wave Extremely sheltered, Sheltered, Very sheltered
Other preferences

Additional Information

None

Species composition

Species found especially in this biotope

    Rare or scarce species associated with this biotope

    -

    Additional information

    None

    Sensitivity reviewHow is sensitivity assessed?

    Sensitivity characteristics of the habitat and relevant characteristic species

    The biotope is defined by the presence of large numbers of the polychaete Capitella capitata (agg.). In very polluted/disturbed areas only Capitella, nematodes and occasional Malacoceros fuliginosus may be found, whilst in slightly less enriched areas and estuaries species such as Tubificoides, Cirriformia tentaculata, Pygospio elegans and Polydora ciliata may also be found. In some areas e.g. the Tees Estuary, high numbers of the polychaete Ophryotrocha may also be present. The sensitivity assessments are based on Capitella capitata as the key defining and characterizing species, although Tubificoides, nematodes, and the polychaetes Pygospio elegans; Polydora ciliata; and Cirriformia tentaculata are considered generally as these are wide-spread, common species.

    Resilience and recovery rates of habitat

    Capitella capitata is a classic opportunist species possessing life history traits of rapid development, many reproductions per year, high recruitment and high death rates (Grassle & Grassle, 1974; McCall, 1977). Experimental studies using defaunated sediments have shown that on small scales Capitella can recolonize to background densities within 12 days (Grassle & Grassle, 1974; McCall, 1977). In Burry Inlet, Wales, tractor towed cockle harvesting led to a reduction in density of some species but Capitella capitata had almost trebled its abundance within the 56 days in a clean sandy area (Ferns et al., 2000).

    In favorable conditions, maturity can be reached in <3 months and growth rate is estimated to be 30 mm per year. Adult potential dispersal is up to 1 km. The species complex displays reproductive variability and planktonic larvae are able to colonize newly disturbed patches but after settlement the species can produce benthic larvae brooded within the adult tube to rapidly increase the population before displacement by more competitive species (Gray, 1979). Bolam & Fernandes (2002) and Shull (1997) noted that Capitella capitata can colonize azoic sediments rapidly in relatively high numbers. Shull (1997) also demonstrated that this occurs by larval settlement, bedload transport and by burrowing. Thus, when conditions are suitable, the time for the community to reach maturity is likely to be less than six months.

    Other speices within the biotope may recolonize more slowly. Tubificid populations tend to be large and to be constant throughout the year, although some studies have noticed seasonal variations (Giere & Pfannkuche, 1982). Many species, including Tubificoides benedii and Baltidrilus costata have a two-year reproductive cycle and only part of the population reproduces each season (Giere & Pfannkuche, 1982). Populations of Tubificoides benedii in the Fourth Estuary have not demonstrated clear seasonality in recruitment (Bagheri & McLusky, 1982), although mature Tubificoides benedii (studied as Peloscolex benedeni) in the Thames Estuary were reported to occur in December with a maximum in late February (Hunter & Arthur, 1978), breeding worms increased from April and maximum cocoon deposition was observed in July (Hunter & Arthur, 1978). Tubificids exhibit many of the traits of opportunistic species; it is dominant, often reaching huge population densities in coastal areas that are enriched in organic matter and is often described as an ‘opportunist’ species adapted to rapid environmental fluctuations and stress (Giere, 2006; Bagheri & McLusky, 1982). However, unlike other opportunist species, it has a long-life span (a few years, Giere, 2006), a prolonged reproductive period from reaching maturity to maximum cocoon deposition, and exhibits internal fertilisation with brooding rather than pelagic dispersal. These factors mean that recolonization is slower than for some opportunistic species such as Capitella capitata and nematodes which may be present in similar habitats.

    Resilience assessment. A Capitella capitata dominated biotope is likely to reach maturity very rapidly because the species of the complex are short lived, reaching maturity within about four months and reproducing throughout the year. Other species within the biotope may colonize more slowly.

    Hydrological Pressures

     ResistanceResilienceSensitivity
    High High Not sensitive
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High

    Capitella capitata is a cosmopolitan species in coastal marine and estuarine soft sediment systems. Grassle & Grassle (1976) used electrophoretic enzyme analysis to determine that the global population is actually made up of several genetically distinct (and apparently genetically isolated) sibling species whose distributions overlap such that local Capitella capitata populations actually consist of a number of co-occurring sibling species. Within the complex, tolerances may vary and local acclimation is possible. Capitella capitata has also been recorded in extreme environments around hydrothermal vents (Gamenick & Giere, 1997), which suggests that the species complex would be relatively tolerant to an increase in temperature.

    Bamber & Spencer (1984) observed that Tubificoides were dominant species in an area affected by thermal discharge in the River Medway estuary. Capitella capitata were seasonal dominants at one station affected by heated effluent. Sediments were exposed to the passage of a temperature front of approximately 10°C between heated effluent and estuarine waters during the tidal cycles.

    Experimental evaluation of the effects of combinations of varying salinities and temperature on Capitella capitata were carried out by Redman (1985) and Warren (1977). Redman (1985) found that length of life decreased as follows: 59 weeks at mid-temperature and salinity (15°C, 25 ppt); 43 weeks at high temperature and high salinity (18°C, 30 ppt); 33 weeks at lower temperature and high salinity (12°C, 30 ppt); 17 weeks at high temperature and low salinity (18°C, 20 ppt). Redman (1985) also found that net reproduction (Ro: the mean number of offspring produced per female at the end of the cohort) decreased as follows: 41.75 control; 36.69 under high salinity, high temperature; 2.19 high temperature, low salinity; 2.16 low temperature, high salinity. Therefore, a combination of changes in temperature and salinity may decrease the viability of the population. Warren (1977) used individual worms collected from Warren Point (south west England) to test response to high and low temperatures. Worms were acclimated to 10°C for 10 days and subsequently heated in a water bath to experienced a rise in temperature of 1°C per 5 min. When the temperature had reached 28°C worms were removed at 0.5°C intervals and returned to a constant temperature of 10°C. The percentage mortality after 24 h was calculated. Larvae were removed from the maternal tube and tested using the same method. The experiments indicated that temperatures above 30°C were most critical; the upper lethal temperature was 31.5°C for adult worms and a little higher for the larvae.

    Sensitivity assessment.  Typical surface water temperatures around the UK coast vary seasonally from 4-19°C (Huthnance, 2010). The biotope, based on the characterizing species, is considered to tolerate a 2°C increase in temperature for a year. The experimental studies by Redman (1985) suggest that changes in temperature may reduce the life-span of Capitella capitata, however, this effect is not considered to alter the character of the biotope as the short life cycle of this species should lead to rapid replenishment of the population. The experiments by Warren (1977) suggest that both the chronic and acute increases in temperature would not exceed the thermal tolerance of Capitella capitata.  The dominance of Tubificoides spp. in sediments exposed to heated effluent suggests that this genus would be highly resistant to an increase in temperature at the pressure benchmark. Biotope resistance based on the characterizing and associated Tubificoides spp. is therefore assessed as ‘High’ and resilience as ‘High’ (by default), so the biotope is considered to be ‘Not sensitive’.

    High High Not sensitive
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High

    Capitella capitata is a cosmopolitan species in coastal marine and estuarine soft sediment systems. Grassle & Grassle (1976) used electrophoretic enzyme analysis to determine that the global population is actually made up of several genetically distinct (and apparently genetically isolated) sibling species whose distributions overlap such that local Capitella capitata populations actually consist of a number of co-occurring sibling species. Within the complex, tolerances may vary and local acclimation is possible. Wu et al. (1988) collected animals at seawater temperatures of -2°C that harboured mature oocytes indicating reproductive activity even under low temperatures.

    Warren (1977) used  individual worms collected from Warren Point (south west England) to test response to high and low temperatures. Worms were acclimated to 10°C for 10 days prior to testing. The worms were cooled in a water bath to experience a decrease in temperature of 1°C per 5 min. When the final temperature was reached, worms were removed at 0.5°C intervals and returned to a constant temperature of 10°C. The percentage mortality after 24 h was calculated. Each experiment was repeated once. Larval Capitella capitata were removed from the maternal tube and tested using the same method. Both adults and larvae were tolerant of low temperatures, 50% of the adults and 65% of the larvae surviving at -1°C.

    Most littoral oligochaetes, including tubificids and enchytraeids, can survive freezing temperatures and can survive in frozen sediments (Giere & Pfannkuche, 1982). Tubificoides benedii (studied as Peloscolex benedeni) recovered after being frozen for several tides in a mudflat (Linke, 1939).

    Sensitivity assessment. Typical surface water temperatures around the UK coast vary, seasonally from 4-19°C (Huthnance, 2010). The biotope, based on the characterizing species, is considered to tolerate a 2°C decrease in temperature for a year. The experiments by Warren (1977) suggest that both the chronic and acute decreases in temperature would not exceed the thermal tolerance of Capitella capitata.  Biotope resistance based on the characterizing and associated Tubificoides spp. is therefore assessed as ‘High’ and resilience as ‘High’ (by default), so the biotope is considered to be ‘Not sensitive’.

    High High Not sensitive
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High

    The biotope occurs in full (30-35 ppt), variable (18-35 ppt) and low salinity (<18 ppt) (JNCC, 2015). Given the wide salinity tolerance, biotopes found in the middle of the range would not be sensitive to an increase from variable to full salinity. No evidence was found to assess an increase in salinity above full.

    Sensitivity assessment. The biotope is considered to have high resistance to a change to full salinity from variable or low, although some mortality may occur before species acclimation. Capitella capitata and other associated species occur intertidally and in areas with limited water exchange such as lagoons; these habitats may experience short term increase sin salinity due to evaporation and some tolerance is therefore expected with local acclimation possible. Biotope resistance to this pressure is therefore assessed as ‘High’ and resilience as ‘High’ (by default), so the biotope is considered to be ‘Not sensitive’.

    High High Not sensitive
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High

    The biotope occurs in full (30-35 ppt), variable (18-35 ppt) and low salinity (<18 ppt). Given the wide salinity tolerance, biotopes found in the middle of the range would not be sensitive to an decrease from variable to low salinity. 

    Warren (1977) used individual worms collected from Warren Point (south-west England) to test response to reduced salinity. Individual Capitella capitata were acclimated to 33 ‰ for 1 week prior to exposure to salinities of 1.5, 5.5, 18 and 33 ‰. Larvae removed from the maternal tube were also tested in groups of 10. The results of tolerance tests showed that adult Capitella capitata acclimated at 33 ‰ were intolerant of reduced salinities below 20 ‰, all exposed adults died within 4 days when exposed at 18 ‰ and within 1 day at 9 ‰. The larvae were more tolerant, living for 10 days at 15.5 ‰ with little apparent ill effect.

    Sensitivity assessment. The biotope is considered to have high resistance to a change to full salinity from variable or low, although some mortality may occur before species acclimation. Capitella capitata and other associated species occur intertidally and in areas with limited water exchange such as lagoons: these habitats may experience short term decreases in salinity due to dilution by rainfall or other freshwater inputs and some tolerance is therefore expected with local acclimation possible. 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’.

    Medium High Low
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High

    Increases and decreases in water velocity may lead to increased erosion or deposition. The associated pressures alteration to sediment type and siltation are assessed separately.  Experimental increases in near-bed current velocity were achieved over intertidal sandflats by placing flumes on the sediment to accelerate water flows (Zuhlke & Reise, 1994). The increased flow led to the erosion of up to 4 cm depth of surface sediments. No significant effect was observed on the abundance of Capitella capitata and numbers of Tubificoides benedii and Tubificoides pseudogaster were unaffected, as they probably avoided suspension by burrowing deeper into sediments. This was demonstrated by the decreased abundance of oligochaetes in the 0-1 cm depth layer and increased abundance of oligochaetes deeper in sediments (Zuhlke & Reise, 1994). A single storm event had a similar result with decreased abundance of oligochaetes in surficial layers, coupled with an increase in deeper sediments (Zuhlke & Reise, 1994). Although Tubificoides spp. can resist short-term disturbances their absence from sediments exposed to higher levels of disturbance indicate that they would be sensitive to long-term changes in sediment mobility (Zuhlke & Reise, 1994). Birtwell & Arthur (1980) reported seasonal changes in abundance in Baltidrilus costata (studied as Tubifex costatus) which they attributed to erosion of the upper sediment layers caused by high river flows and wave action.

    In the turbid waters of estuaries, where many mud habitats develop, a reduction in water flow is likely to result in a significant increase in siltation increasing the silt and clay content of the substratum. Decreases in water flow with increased siltation of fine particles are considered unlikely to alter the physical character of this habitat type as it is already found in sheltered areas where siltation occurs and where particles are predominantly fine. Reductions in waterflow occurring through the presence of trestles (for off-bottom oyster cultivation) arranged in parallel rows in the intertidal area (Goulletquer & Héral, 1997), reducing the strength of tidal currents (Nugues et al., 1996) has been observed to limit the dispersal of pseudofaeces and faeces in the water column and thus increase the natural sedimentation process by several orders of magnitude (Ottman & Sornin, 1985, summarised in Bouchet & Sauriau, 2008). As the characterizing Capitella capitata oligochaetes can live relatively deeply buried and in depositional environments with low water flows (based on habitat preferences) and low oxygenation, they are considered to be not sensitive to decreases in water flow.

    Sensitivity assessment. Where increased or decreased water flows altered the sediment type, this could lead to sediment reclassification and thus change is assessed in the sedimentary change assessment. As muds tend to be cohesive and the surface tends to be smooth reducing turbulent flow, an increase at the pressure benchmark may not lead to increased erosion. The biotope resistance is assessed as ‘Medium’ as a precautionary assessment, resilience is assessed as ‘High’ (following restoration of usual conditions) and sensitivity is assessed as ‘Low’. The biotope is not considered to be sensitive to decreased flows due to its presence in sheltered habitats and the tolerance of Tubificoides benedii for low oxygen and sediment deposition.

    Not relevant (NR) Not relevant (NR) Not relevant (NR)
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR

    'Not relevant' to subtidal biotopes.

    High High Not sensitive
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High

    This biotope occurs in habitats that are sheltered from strong wave action. Disturbance of sediment by waves may reduce  oligochaete abundance (Giere, 1977) and oligochaetes may be absent from very wave exposed shores (Giere & Pfannkuche, 1982 and references therein).  As this biotope occurs across three wave exposure categories; sheltered, extremely sheltered and very sheltered (JNCC, 2015), this is considered to indicate that mid-range biotopes would tolerate both an increase and decrease in wave exposure at the pressure benchmark. Resistance is therefore assessed as ‘High’ and resilience as ‘High’ by default and the biotope is considered to be ‘Not sensitive’.

    Chemical Pressures

     ResistanceResilienceSensitivity
    Not relevant (NR) Not relevant (NR) Not sensitive
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR

    'Not sensitive' at the pressure benchmark that assumes compliance with all relevant environmental protection standards.

    Contamination at levels exceeding the pressure benchmark may have negative effects. High levels of organic material in intertidal muds, coupled with sub-surface anoxia, may sequester metals reducing bioavailability and hence reducing toxicity. However, sediment disturbance and exposure to oxygenated waters will render metals labile and bioavailable.

    Experimental studies with various species suggest that polychaete worms are quite tolerant to heavy metals (Bryan, 1984). High numbers of Capitella capitata have been recorded in areas containing high metal concentrations (Petrich & Reish, 1979; Ward & Young, 1982; Olsgard, 1999), although abundance of Capitella capitata in Norway has also been noted to have a significant negative correlation between sediment content of Cu and abundance of the species, with an obvious reduction in abundance at approximately 900 ppm Cu (Olsgard, 1999). Some impacts on population size and reproduction of Capitella capitata as a result of metal pollution, both in the field and the laboratory, have been observed.

    Tests of copper toxicity have been carried out on the characterizing species Capitella capitata. Laboratory tests carried out in water may not reflect sediment conditions where, again, copper toxicity and exposure is determined by a number of parameters including the degree to which it is adsorbed on to particles selected as food for deposit feeders. A 2-year microcosm experiment was undertaken to investigate the impact of copper on the benthic fauna of the lower Tyne Estuary (UK) by Hall & Frid (1995). During a 1-year simulated contamination period, 1 mg/l copper was supplied at 2-weekly 30% water changes, at the end of which the sediment concentrations of copper in contaminated microcosms reached 411 μg/g. Toxicity effects reduced populations of the four dominant taxa, including Capitella capitata. When copper dosage was ceased and clean water supplied, sediment copper concentrations fell by 50% in less than 4 days, but faunal recovery took up to 1 year, with the pattern varying between taxa. Since the copper leach rate was so rapid it is concluded that after remediation, contaminated sediments show rapid improvements in chemical concentrations, but faunal recovery may be delayed with experiments in microcosms showing faunal recovery taking up to a year.

    Rygg (1985) classified Capitella capitata as a highly tolerant species, common at the most copper polluted stations (copper >200 mg/kg) in Norwegian fjords. 

    Not relevant (NR) Not relevant (NR) Not sensitive
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR

    'Not sensitive' at the pressure benchmark that assumes compliance with all relevant environmental protection standards.

    Contamination at levels exceeding the pressure benchmark may have negative effects. 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. However, high numbers of Capitella capitata have been recorded in hydrocarbon contaminated sediments (Ward & Young, 1982; Olsgard, 1999; Petrich & Reish, 1979) and colonization of areas defaunated by high hydrocarbon levels may be rapid (Le Moal, 1980). After a major spill of fuel oil in West Virginia, Capitella increased dramatically alongside large increases in Polydora ligni and Prionospio sp. (Sanders et al., 1972 cited in Gray, 1979). Experimental studies adding oil to sediments have found that Capitella capitata increased in abundance initially, although it was rarely found in samples prior to the experiment (Hyland, 1985).

    Capitella capitata is able to withstand relatively high hydrocarbon concentrations and may even take advantage of any available space, caused by mortality of other species.

    In Finland, in oligohaline inland waters near an oil refinery, Baltidrilus costata (as Tubifex costatus) appeared to be sensitive to oil pollution and had completely disappeared from sediments exposed to pollution and did not recolonise during a 4 year post-pollution period (Leppäkoski & Lindström, 1978). Tubificoides benedii appears to be more tolerant and was found in UK waters near oil refineries as the sole surviving member of the macrofauna. Populations were however apparently reduced and the worms were absent from areas of oil discharge and other studies indicate sensitivity to oiling (Giere & Pfannkuche, 1982 and references therein).

    Not relevant (NR) Not relevant (NR) Not sensitive
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR

    'Not sensitive' at the pressure benchmark that assumes compliance with all relevant environmental protection standards.

    Mendez (2006) showed that the effects of exposing the deposit feeding polychaete Capitella to sediment spiked with environmentally relevant concentrations of teflubenzuron (another chemical used to control infestations of sea lice) caused mortality in one species of Capitella and reduced the egestion rate of another. 

    No evidence (NEv) No Evidence (NEv) No evidence (NEv)
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR

    No evidence.

    Not relevant (NR) Not relevant (NR) Not sensitive
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR

    'Not sensitive' at the pressure benchmark that assumes compliance with all relevant environmental protection standards.

    High High Not sensitive
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High

    Capitella capitata exhibits a relatively high tolerance for sediment hypoxia, hydrogen sulphide concentration, and other sediment conditions avoided by many infauna (Henriksson, 1969). Forbes & Lopez (1990) experimentally demonstrated that reduced oxygen concentrations (pO2 = 20 mm Hg or less) led to decreased Capitella capitata growth rates and cessation of burrowing and feeding activity even when an abundance of food was provided. The authors hypothesize that animals rely solely on anaerobic metabolism once this threshold is crossed. Magnum & Van Winkle (1973) similarly observed that Capitella capitata oxygen uptake ceased when pO2 fell to between 0-34 mm Hg. The fact that experimental worms lost body mass under these conditions supports the contention that full aerobic metabolism cannot be sustained at very low ambient oxygen conditions despite a very high affinity of Capitella capitata hemoglobin for oxygen.

    Tubificoides benedii has a high capacity to tolerate anoxic conditions, its extreme oxygen tolerance is based on an unusually low respiration rate (Giere et al., 1999).  Respiration rates of Tubificoides benedii measured at various oxygen concentrations showed that aerobic respiration is maintained even at very low oxygen concentrations (Giere et al., 1999). Birtwell & Arthur (1980) showed that Tubificoides benedii could tolerate anoxia in the Thames Estuary (LT50 = 58.8 hours at 20°C, 26.6 hours at 25°C  and 17.8 hours at 30°C in experiments with worms acclimated to 20°C).

    Sensitivity assessments. Based on the reported tolerances for anoxia for Capitella capitata and Tubificoides, biotope resistance is assessed as ‘High’, resilience is assessed as ‘High’ (by default) and the biotope is considered to be ‘Not sensitive’.

    High High Not sensitive
    Q: Low
    A: NR
    C: NR
    Q: High
    A: High
    C: High
    Q: Low
    A: Low
    C: Low

    In very sheltered areas, green algae such as Enteromorpha spp. may form mats on the surface of the mud during the summer months, particularly if nutrient enrichment occurs.

    Sensitivity assessment. As the benchmark is relatively protective and would not lead to blooms of Enteromorpha spp. (although green algae may be present on the surface layers of sediments in the summer), biotope resistance is assessed as ‘High’, resilience is assessed as ‘High’ and the biotope is considered to be ‘Not sensitive’.

    High High Not sensitive
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High

    Benthic responses to organic enrichment have been described by Pearson & Rosenberg (1978) and Gray (1981).  In general, moderate enrichment increases food supply and increases productivity and abundance. Dense Capitella capitata populations are frequently located in areas with greatly elevated organic content such as areas of sewage disposal and below fish farms and mussel long lines, even though eutrophic sediments are often anoxic and highly sulfidic (Gray, 1979; Tenore, 1977; Warren, 1977; Tenore & Chesney, 1985; Bridges et al., 1994; Haskoning, 2006; Callier et al., 2007)

    Benthic fauna underneath floating salmon farm cages in a Scottish sea loch showed marked changes in species number, diversity, faunal abundance and biomass in the region of the fish farm (Brown et al., 1987). Four ‘zones’ of effect were identified: in zone 1 directly beneath and up to the edge of the cages there was an azoic zone; in zone 2, from the edge of the cages out to 8 m, the sediments were highly enriched and dominated by Capitella capitella and Scolelepis fuliginosa. Kutti et al. (2008) studied organic enrichment of sediments below a fish farm in a fjord system (Norway), during periods of high organic loading production was mostly by Capitella capitata. The threshold for increased infauna production in this deep benthic ecosystem had been reached at an annual flux of 500 g C/m2 and continuous loadings at this magnitude over time might cause organic overloading of fish farm sediments.

    The oligochaetes Tubificoides benedii and Baltidrilus costatus are both very tolerant of high levels of organic enrichment and often dominate sediments where sewage has been discharged or other forms of organic enrichment have occurred (Pearson & Rosenberg, 1978; Gray, 1971; McLusky et al., 1980).

    Sensitivity assessment. Above evidence indicates that increased organic matter levels associated with aquaculture can favour Capitella capitata and Tubificoides spp., resistance is therefore considered to be ‘High’, resilience ‘High’ (by default) and the species is ‘Not sensitive’. It should be noted, however, that sensitivity is greater to gross organic enrichment levels within the spatial footprint of activities.

    Physical Pressures

     ResistanceResilienceSensitivity
    None Very Low High
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High

    All marine habitats and benthic species are considered to have a resistance of ‘None’ to this pressure and to be unable to recover from a permanent loss of habitat (resilience is ‘Very Low’). Sensitivity within the direct spatial footprint of this pressure is therefore ‘High’. Although no specific evidence is described, confidence in this assessment is ‘High’ due to the incontrovertible nature of this pressure.

    None Very Low High
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High

    The biotope is characterized by the sedimentary habitat (JNCC, 2015), and 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 Capitella capitata, other polychaetes and oligochaetes that live buried within the sediment.

    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’. 

    None Very Low High
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High
    Q: High
    A: High
    C: High

    Capitella capitata can survive in a range of habitats including fine sands and areas with boulders, a change in sediment type was not judged to completely reduce habitat suitability for this species. An increase of sediment coarseness to sand would not exclude this species, based on published habitat preferences, but may have population level effects as habitat suitability may be reduced. Recovery would depend on the return of previous habitat conditions.

    Tubificoides benedii (studied as Peloscolex benedeni) are found in a range of substratum types from sandy mixed habitats, fine sands and coarse sands (Giere & Pfannkuche, 1982 and references therein). Giere & Pfannkuche (1982) suggest that factors that correlate to substratum types such as organic matter availability, size and shape of the intertstitial space between grains, the level of sediment disturbance and water content, rather than the sediment type alone are the key factors influencing distribution.

    Sensitivity assessment. A change in sediment type to mixed or coarser particles could lead to changes in the density of Capitella capitata, other burrowing polychaetes and oligochaetes depending on species specific responses. However, the loss of the muddy sediment  that characterizes this habitat would change the character of the biotope, the characterizing species, with potentially an increase in bivalves or crustaceans and is likely to lead to reclassification. Based on a change in character, the biotope is considered to have ‘No’ resistance to this pressure, resilience is assessed as 'Very Low’ as a change at the pressure benchmark is permanent and biotope sensitivity is assessed as ‘High’.

    None High Medium
    Q: High
    A: High
    C: High
    Q: High
    A: Low
    C: High
    Q: High
    A: Low
    C: High

    Sedimentary communities are likely to be highly intolerant of substratum removal, which will lead to partial or complete defaunation, exposure of underlying sediment which may be anoxic and/or of a different character or bedrock and lead to changes in the topography of the area (Dernie et al., 2003). Any remaining species, given their new position at the sediment/water interface, may be exposed to conditions to which they are not suited. Removal of 30 cm of surface sediment will remove the polychaete and oligochaete community and other species present in the biotope. Recovery of the biological assemblage may take place before the original topography is restored, if the exposed, underlying sediments are similar to those that were removed. Hydrodynamics and sedimentology (mobility and supply) influence the recovery of soft sediment habitats (Van Hoey et al., 2008).

    Sensitivity assessment. Extraction of 30 cm of sediment will remove the characterizing biological component of the biotope. Resistance is assessed as ‘None’ and biotope resilience is assessed as ’High’’. Biotope sensitivity is therefore ‘Medium’. 

    Medium High Low
    Q: High
    A: Medium
    C: Medium
    Q: High
    A: Medium
    C: High
    Q: High
    A: Medium
    C: Medium

    Capitella capitata is a soft bodied, relatively fragile species inhabitaing mucus tubes close to the sediment surface. Abrasion and compaction of the surficial layer may damage individuals. Capitella capitata and Pygospio elegans have been categorised through literature and expert reviews as AMBI fisheries Group IV- 'A second-order opportunistic species, which are sensitive to fisheries in which the bottom is disturbed. Their populations recover relatively quickly however and benefit from the disturbance, causing their population sizes to increase significantly in areas with intense fisheries' (Gittenberger & Van Loon, 2011). Chandrasekara & Frid (1996) found that in intertidal muds, along a pathway heavily used for five summer months (ca 50 individuals a day), some species including Capitella capitata and Scoloplos armiger reduced in abundance. Bonsdorff & Pearson (1997) found that sediment disturbance forced Capitella capitata deeper into the sediment, although the species was able to burrow back through the sediment to the surface again. 

    Tubificoides benedii can be relatively deeply buried and could avoid direct exposure to abrasion although sediment disturbance and compaction could damage these soft-bodied species. Oligochaetes in general are not found in high abundances in sediments with high levels of disturbance from wave action. 

    Sensitivity assessment. Abrasion may damage or kill a proportion of the population of the characterizing Capitella capitata and associated species. Tubificoides spp. that are generally buried more deeply within sediments are likely to be more resistant than species such as Pygospio elegans that inhabit fragile tubes that extend above the sediment surface. Biotope resistance is assessed as 'Medium' and resilience as 'High', so sensitivity is assessed as 'Low'.

    Low High Low
    Q: High
    A: High
    C: Low
    Q: High
    A: Medium
    C: High
    Q: High
    A: Medium
    C: Low

    Rabaut et al. (2008) found that beam trawling on intertidal Lanice conchilega reefs reduced the abundance of Capitella capitata.  Ferns et al. (2000), however, found that tractor-towed cockle harvesting had little effect on Capitella capitata, but species that are present at the surface were more badly affected. The tractor dredging removed 83% of Pygospio elegans (initial density 1850/m2). These results are supported by work by Moore (1991) and Rostron (1995) who also found that cockle dredging can result in reduced densities of some polychaete species, including Pygospio elegans.

    Whomersley et al. (2010) conducted experimental raking on intertidal mudflats at two sites (Creeksea Crouch Estuary, England and Blackness lower Forth Estuary, Scotland), where Tubificoides benedii were dominant species. For each treatment, 1 m2 plots were raked twice to a depth of 4 cm (using a garden rake). Plots were subject to either low intensity treatments (raking every four weeks) or high (raking every two weeks). The experiment was carried out for 10 months at Creeksea and a year at Blackness. The high and low raking treatments appeared to have little effect on Tubificoides benedii (Whomersley et al., 2010). These results are supported by observations that two experimental passes of an oyster dredge that removed the sediment to a depth of between 15-20 cm did not significantly affect Tubifcoides benedii (EMU, 1992).

    Sensitivity assessment. Capitella capitata is present in the surface layers of sediment and may be damaged, displaced or killed by penetration and disturbance of the sediment. Resistance is assessed as ‘Low’ and resilience as ‘High’, so sensitivity is assessed as ‘Low’.

    Medium High Low
    Q: Low
    A: NR
    C: NR
    Q: High
    A: Low
    C: High
    Q: Low
    A: Low
    C: Low

    Estuaries, where this biotope is often found, can be naturally turbid systems due to sediment resuspension by wave and tide action and inputs of  high levels of suspended solids, transported by rivers. The level of suspended solids depends on a variety of factors including: substrate type, river flow, tidal height, water velocity, wind reach/speed and depth of water mixing (Parr et al., 1998). Transported sediment including silt and organic detritus can become trapped in the system where the river water meets seawater. Dissolved material in the river water flocculates when it comes into contact with the salt wedge pushing its way upriver. These processes result in elevated levels of suspended particulate material with peak levels confined to a discrete region (the turbidity maximum), usually in the upper-middle reaches, which moves up and down the estuary with the tidal ebb and flow. Intertidal mudflats depend on the supply of particulate matter to maintain mudflats and the associated biological community is exposed naturally to relatively high levels of turbidity/particulate matter. 

    Sensitivity assessment. The biological assemblage characterizing this biotope is infaunal and consists of sub-surface deposit feeders. Increased suspended solids are unlikely to have an impact and resistance is assessed as ‘High’ and resilience as ‘High’, so the biotope is considered to be ‘Not sensitive’. A reduction in suspended solids may reduce deposition and supply of organic matter, resistance to a decrease is therefore assessed as ‘Medium’, as a shift between deposition and erosion could result in the net loss of surficial sediments. A reduction in organic matter as suspended solids could also reduce production within this biotope. Resistance is assessed as ‘Medium’, as over a year the impact may be relatively small, and resistance is assessed as ‘High’, following restoration of usual conditions. Biotope sensitivity is therefore assessed as ‘Low’. 

    Low High Low
    Q: High
    A: Medium
    C: Medium
    Q: High
    A: Low
    C: High
    Q: High
    A: Low
    C: Medium

    Subtidal mudflats occur in sheltered environments and, in general, are accreting environments meaning that deposition rather than erosion is the dominant process, this means that the assemblages present (primarily deposit feeders) are adapted to natural levels of siltation through life history traits and can withstand burial (by repositioning in sediment or similarly extending tubes or feeding and respiration structures above the sediment surface). Capitella capitata has been categorised through expert and literature review, as AMBI sedimentation Group IV – 'A second-order opportunistic species, insensitive to higher amounts of sedimentation. Although they are sensitive to strong fluctuations in sedimentation, their populations recover relatively quickly and even benefit. This causes their population sizes to increase significantly in areas after a strong fluctuation in sedimentation' (Gittenberger & van Loon, 2011).The effects of siltation will depend on the amount and rate that particles are added. Capitella capitata is sedentary and adults are judged unlikely to have any mechanism to escape from large inputs. A deep covering of sediment will prevent feeding. Where inputs are at low rates and similar to background sediments then adults may be able to extend tubes to reach the surface to feed.

    Pygospio elegans is limited by high sedimentation rates (Nugues et al., 1996) and the species does not appear to be well adapted to oyster culture areas where there are high rates of accumulation of faeces and pseudo faeces (Sornin et al., 1983; Deslous-Paoli et al., 1992; Mitchell, 2006; Bouchet & Sauriau, 2008).  

    Tubificoides live relatively deeply buried and can tolerate periods of low oxygen that may occur following the deposition of a fine layer of sediment. In addition, the presence of this species in areas experiencing deposition, such as estuaries, indicate that this species is likely to have a high tolerance to siltation events. Tubificoides spp. showed some recovery through vertical migration following the placement of a sediment overburden 6cm thick on top of sediments (Bolam, 2011).

    Whomersley et al. (2010) experimentally buried plots on intertidal mudflats at two sites (Creeksea Crouch Estuary, England and Blackness lower Forth Estuary, Scotland), where Tubificoides benedii were dominant species. For each treatment, anoxic mud was spread evenly to a depth of 4 cm on top of each treatment plot. The mud was taken from areas adjacent to the plots, and was obtained by scraping off the surface oxic layer and digging up the underlying mud from approximately 20 cm depth. Plots were subject to either low intensity treatments (burial every four weeks) or high (burial every two weeks). The experiment was carried out for 10 months at Creeksea and a year at Blackness. At Creeksea numbers of Tubificoides benedii increased in both burial treatments until the third month (high burial) and sixth month (low burial). At Blackness increased numbers ofTubificoides benedii were found in both burial treatments after one month (Whomersley et al., 2010).

    Sensitivity assessment.  Biotope resistance to siltation based on Capitella capitata is judged to be 'Low' with regard to the rapid addition of silts to a depth of <5 cm. Resilience is assessed as 'High' recovery is predicted to be rapid. Sensitivity is therefore assessed as ‘Low’. At lower levels of siltation, sensitivity will be likely to be lower. 

    Low High Low
    Q: Low
    A: NR
    C: NR
    Q: High
    A: Low
    C: High
    Q: Low
    A: Low
    C: Low

    The pressure benchmark (30 cm deposit) represents a significant burial event and the deposit may remain for some time in a sheltered mudflat. Capitella capitata populations are likely to be significantly impacted. Some impacts on Tubificoides benedii and other  oligochaetes may occur and it is considered unlikely that signficiant numbers of the population could reposition, based on (Bolam, 2011). Placement of the deposit will, therefore, result in a defaunated habitat until the deposit is recolonized. Biotope resistance is therefore assessed as 'Low' as some removal of deposit and vertical migration through the deposit may occur. Resilience is assessed as 'High' as migration and recolonization of Capitella capitata and oligochaetes is likely to occur within two years, biotope sensitivity is therefore assessed as 'Low'.

    Not Assessed (NA) Not Assessed (NA) Not assessed (NA)
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR

    Not assessed.

    No evidence (NEv) No Evidence (NEv) No evidence (NEv)
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR

    No evidence.

    Not relevant (NR) Not relevant (NR) Not relevant (NR)
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR

    'Not relevant'.

    Not relevant (NR) Not relevant (NR) Not relevant (NR)
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR

    As the characterizing biological assemblage occurs within the sediment and can be deeply buried (to 10 cm or more), an increase in light or shading is considered ‘Not relevant’. However, shading may reduce the microphytobenthos component of this infralittoral biotope. Mucilaginous secretions produced by these algae may stabilize fine substrata (Tait & Dipper, 1998). Shading will prevent photosynthesis leading to death or migration of sediment microalgae, which may alter sediment cohesion and food supply to higher trophic levels. As this biotope occurs in areas of high turbidity, where light penetration may be limited, an increase in shading is not considered to significantly alter the character of the habitat.

    High High Not sensitive
    Q: Low
    A: NR
    C: NR
    Q: High
    A: High
    C: High
    Q: Low
    A: Low
    C: Low

    The key characterizing species Capitella capitata and the associated species Pygospio elegans are capable of both benthic and pelagic dispersal. In the sheltered waters where this biotope occurs, with reduced water exchange, in-situ reproduction may maintain populations rather than long-range pelagic dispersal. As the tubificid oligochaetes that characterize this biotope have benthic dispersal strategies (via egg cocoons laid on the surface (Giere & Pfannkuche, 1982)), water transport is not a key method of dispersal over wide distances. 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 (NR) Not relevant (NR) Not relevant (NR)
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR

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

    Not relevant (NR) Not relevant (NR) Not relevant (NR)
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR

    Visual disturbance is not considered relevant to this biotope.

    Biological Pressures

     ResistanceResilienceSensitivity
    Not relevant (NR) Not relevant (NR) Not relevant (NR)
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR

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

    None Very Low High
    Q: High
    A: Low
    C: NR
    Q: Low
    A: NR
    C: NR
    Q: Low
    A: Low
    C: Low

    No evidence found.Invasion by the slipper limpet Crepidula fornicata may lead to biotope reversion to  SS.SMx.SMxVS.CreMed suggesting high intolerance as the original biotope would be lost. Species richness might decline as Crepidula may dominate the seabed. Experimental relaying of mussels on intertidal fine sand sediments increased fine sediment proportions and led to colonization by Capitella capitata (Ragnarsson & Rafaelli, 1999), so that sediment modification by bivalves may not render habitats unsuitable for Capitella capitata.

    Sensitivity assessment. Reclassification of the biotope following invasion would result in loss of the biotope, resistance is therefore assessed as 'None', as recovery will not occur until the invasive species is eradicated, recovery is assessed as 'Very Low' and biotope sensitivity is 'High'.

    High High Not sensitive
    Q: Low
    A: NR
    C: NR
    Q: High
    A: High
    C: High
    Q: Low
    A: Low
    C: Low

    Marine oligochaetes host numerous protozoan parasites without apparent pathogenic effects even at high infestation levels (Giere & Pfannkuche, 1982 and references therein).

    Sensitivity assessment. Based on the lack of evidence for mass mortalities in Capitella capitata and oligochaetes from microbial pathogens, resistance is assessed as ‘High’ and resilience as ‘High’ (by default), so that the biotope is assessed as ‘Not sensitive’.

    Not relevant (NR) Not relevant (NR) Not relevant (NR)
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR
    Q: NR
    A: NR
    C: NR

    No characterizing species within the biotope are targeted by commercial or recreational fishers or harvesters. This pressure is therefore considered ‘Not relevant’.

    Low High Low
    Q: Low
    A: NR
    C: NR
    Q: High
    A: Low
    C: High
    Q: Low
    A: Low
    C: Low

    Incidental removal of the characterizing species would alter the character of the biotope and the delivery of ecosystem services such as secondary production and bioturbation. Populations of oligochaetes provide food for macroinvertebrates fish and birds. For example, up to 67% of flounder and plaice stomachs examined from the Medway Estuary (UK) (Van den Broek, 1978) contained the remains of Tubificoides benedii (studied as Peloscolex benedeni) and shrimps which in turn support higher trophic levels (predatory birds and fish). For some migratory birds, the characterizing species Tubificoides benedii can form an important part of the diet during winter (Bagheri & McLusky, 1984). Polychaetes and crustaceans are also predators of oligochaetes and may significantly reduce numbers (Giere & Pfannkuche, 1982 and references therein). The loss of the oligochaete population could, therefore, impact other trophic levels.

    Sensitivity assessment. Removal of the characterizing species would alter the character of the biotope. Resistance is therefore assessed as ‘Low’ and resilience as ‘High’, so sensitivity is categorized as ‘Low’.

    Importance review

    Policy/Legislation

    UK Biodiversity Action Plan Priority

    Exploitation

    Capitella capitata has no commercial value and so is unlikely to be subject to exploitation.

    Additional information

    -

    Bibliography

    1. Bagheri, E. & McLusky, D., 1982. Population dynamics of oligochaetes and small polychaetes in the polluted forth estury ecosystem. Netherlands Journal of Sea Research, 16, 55-66.

    2. Bagheri, E.A. & McLusky, D.S., 1984. The oxygen consumption of Tubificoides benedeni (Udekem) in relation to temperature and its application to production biology. Journal of Experimental Marine Biology and Ecology, 78, 187-197.
    3. Bamber, R.N. & Spencer, J.F. 1984. The benthos of a coastal power station thermal discharge canal. Journal of the Marine Biological Association of the United Kingdom, 64, 603-623.
    4. Barnes, R.S.K., 1994. The brackish-water fauna of northwestern Europe. Cambridge: Cambridge University Press.
    5. Birtwell, I.K. & Arthur, D.R., 1980. The ecology of tubificids in the Thames Estuary with particular reference to Tubifex costatus (Claparède). In Proceedings of the first international symposium on aquatic oligochaete biology, Sydney, British Colombia, Canada, May 1-4, 1979. Aquatic oligochaete biology (ed. R.O. Brinkhurst & D.G. Cook), pp. 331-382. New York: Plenum Press
    6. Bolam, S.G. & Fernandes, T.F., 2002. Dense aggregations of tube-building polychaetes: response to small-scale disturbances. Journal of Experimental Marine Biology and Ecology, 269, 197-222.
    7. Bonsdorff, E. & Pearson, T.H., 1997. The relative impact of physical disturbance and predation by Crangon crangon on population density in Capitella capitella: An experimental study. Ophelia, 46, 1-10.
    8. Bouchet, V.M. & Sauriau, P.-G., 2008. Influence of oyster culture practices and environmental conditions on the ecological status of intertidal mudflats in the Pertuis Charentais (SW France): A multi-index approach. Marine Pollution Bulletin, 56 (11), 1898-1912.
    9. Bouchet, V.M. & Sauriau, P.-G., 2008. Influence of oyster culture practices and environmental conditions on the ecological status of intertidal mudflats in the Pertuis Charentais (SW France): A multi-index approach. Marine Pollution Bulletin, 56 (11), 1898-1912.
    10. Bridges, T.S., 1996. Effects of organic additions to sediment, and maternal age and size, on patterns of offspring investment and performance in two opportunistic deposit-feeding polychaetes. Marine Biology, 125, 345-357.
    11. Bridges, T.S., Levin, L.A., Cabrera, D. & Plaia, G., 1994. Effects of sediment amended with sewage, algae, or hydrocarbons on growth and reproduction in two opportunistic polychaetes. Journal of Experimental Marine Biology and Ecology, 177 (1), 99-119.
    12. Brown, J., Gowen, R. & McLusky, D., 1987. The effect of salmon farming on the benthos of a Scottish sea loch. Journal of Experimental Marine Biology and Ecology, 109 (1), 39-51.

    13. Bryan, G.W., 1984. Pollution due to heavy metals and their compounds. In Marine Ecology: A Comprehensive, Integrated Treatise on Life in the Oceans and Coastal Waters, vol. 5. Ocean Management, part 3, (ed. O. Kinne), pp.1289-1431. New York: John Wiley & Sons.
    14. Callier, M. D., McKindsey, C.W. & Desrosiers, G., 2007. Multi-scale spatial variations in benthic sediment geochemistry and macrofaunal communities under a suspended mussel culture. Marine Ecology Progress Series, 348, 103-115.

    15. Cardell, M.J., Sarda, R. & Romero, J., 1999. Spatial changes in sublittoral soft-bottom polychaete assemblages due to river inputs and sewage discharges. Acta Oecologica, 20, 343-351.

    16. Chandrasekara, W.U. & Frid, C.L.J., 1996. Effects of human trampling on tidal flat infauna. Aquatic Conservation: Marine and Freshwater Ecosystems, 6, 299-311.
    17. Cuomo, M.C., 1985. Sulphide as a larval settlement cue for Capitella sp. I. Biogeochemistry, 1, 169-181.
    18. Dernie, K.M., Kaiser, M.J., Richardson, E.A. & Warwick, R.M., 2003. Recovery of soft sediment communities and habitats following physical disturbance. Journal of Experimental Marine Biology and Ecology, 285-286, 415-434.
    19. Deslous-Paoli, J.-M., Lannou, A.-M., Geairon, P., Bougrier, S., Raillard, O. & Héral, M., 1992. Effects of the feeding behavior of Crassostrea gigas (Bivalve Molluscs) on biosedimentation of natural particulate matter. Hydrobiologia, 231 (2), 85-91.
    20. Eagle, R.A. & Rees, E.I.S., 1973. Indicator species - a case for caution. Marine Pollution Bulletin, 4, 25.
    21. EMU, 1992. An experimental study on the impact of clam dredging on soft sediment macro invertebrates. English Nature Research Reports. No 13.

    22. Ferns, P.N., Rostron, D.M. & Siman, H.Y., 2000. Effects of mechanical cockle harvesting on intertidal communities. Journal of Applied Ecology, 37, 464-474.
    23. Flach, E.C., 1991. Disturbance of benthic infauna by sediment-reworking activities of the lugworm Arenicola marina. Netherlands Journal of Sea Research, 30, 81-89.
    24. Forbes, T.L. & Lopez, G.R., 1990. The effect of food concentration, body size, and environmental oxygen tension on the growth of the deposit-feeding polychaete, Capitella species 1. Limnology and Oceanography, 35 (7), 1535-1544.
    25. Gamenick, I. & Giere, O., 1997. Ecophysiological studies on the Capitella capitata complex: respiration and sulfide exposure. Bulletin of Marine Science, 60, 613.
    26. Giere, O., 1977. An ecophysiological approach to the microdistribution of meiobenthic Oligochaeta. I. Phallodrilus monospermathecus (Knöllner)(Tubificidae) from a subtropical beach at Bermuda. Biology of benthic organisms. Pergamon Press New York, 285-296.

    27. Giere, O., 2006. Ecology and biology of marine oligochaeta–an inventory rather than another review. Hydrobiologia, 564 (1), 103-116.

    28. Giere, O. & Pfannkuche, O., 1982. Biology and ecology of marine Oligochaeta, a review. Oceanography and Marine Biology, 20, 173-309.

    29. Giere, O., Preusse, J. & Dubilier, N. 1999. Tubificoides benedii (Tubificidae, Oligochaeta) - a pioneer in hypoxic and sulfide environments. An overview of adaptive pathways. Hydrobiologia, 406, 235-241.
    30. Gittenberger, A. & Van Loon, W.M.G.M., 2011. Common Marine Macrozoobenthos Species in the Netherlands, their Characterisitics and Sensitivities to Environmental Pressures. GiMaRIS report no 2011.08.
    31. Gittenberger, A. & Van Loon, W.M.G.M., 2011. Common Marine Macrozoobenthos Species in the Netherlands, their Characterisitics and Sensitivities to Environmental Pressures. GiMaRIS report no 2011.08.
    32. Goulletquer, P. & Heral, M., 1997. Marine molluscan production trends in France: from fisheries to aquaculture. NOAA Tech. Rep. NMFS, 129.

    33. Grassle, J.F. & Grassle, J.P., 1974. Opportunistic life histories and genetic systems in marine benthic polychaetes. Journal of Marine Research, 32, 253-284.
    34. Grassle, J.F. & Grassle, J.P., 1976. Sibling species in the marine pollution indicator (Capitella) (Polychaeta). Science, 192, 567-569.
    35. Grassle, J.F. & Grassle, J.P., 1978. Life histories and genetic variation in marine invertebrates. In Marine organisms: genetics, ecology and evolution (ed. B. Battaglia & J.A. Beardmore), pp. 347-364. New York: Plenum Press.
    36. Gray, J.S., 1971. The effects of pollution on sand meiofauna communities. Thalassia Jugoslovica, 7, 76-86.
    37. Gray, J.S., 1979. Pollution-induced changes in populations. Philosophical Transactions of the Royal Society of London, Series B, 286, 545-561.
    38. Gray, J.S., 1981. The ecology of marine sediments. An introduction to the structure and function of benthic communities. Cambridge: Cambridge University Press.
    39. Hall, J.A. & Frid, C.L.J., 1995. Response of estuarine benthic macrofauna in copper-contaminated sediments to remediation of sediment quality. Marine Pollution Bulletin, 30, 694-700.
    40. Haskoning UK Ltd. 2006. Investigation into the impact of marine fish farm deposition on maerl beds. Scottish Natural Heritage Commissioned Report No. 213 (ROAME No. AHLA10020348).

    41. Henriksson, R., 1969. Influence of pollution on the bottom fauna of the Sound (Öresund). Oikos, 20 (2), 507-523.
    42. Holte, B. & Oug, E., 1996. Soft-bottom macrofauna and responses to organic enrichment in the subarctic waters of Tromsoe, northern Norway. Journal of Sea Research, 36, 227-237.
    43. Hunter, J., & Arthur, D.R., 1978. Some aspects of the ecology of Peloscolex benedeni Udekem (Oligochaeta: Tubificidae) in the Thames estuary. Estuarine and Coastal Marine Science, 6, 197-208.
    44. Huthnance, J., 2010. Ocean Processes Feeder Report. London, DEFRA on behalf of the United Kingdom Marine Monitoring and Assessment Strategy (UKMMAS) Community.
    45. Hyland, J.L., Hoffman, E.J. & Phelps, D.K., 1985. Differential responses of two nearshore infaunal assemblages to experimental petroleum additions. Journal of Marine Research, 43 (2), 365-394.
    46. JNCC, 2015. The Marine Habitat Classification for Britain and Ireland Version 15.03. JNCC: JNCC. 2015(20/05/2015). jncc.defra.gov.uk/MarineHabitatClassification
    47. Karakassis, I., Tsapakis, M., Hatziyanni, E., Papadopoulou, K. & Plaiti, W., 2000. Impact of cage farming of fish on the seabed in three Mediterranean coastal areas. ICES Journal of Marine Science, 57, 1462-1471.
    48. Kutti, T., Ervik, A. & Høisæter, T., 2008. Effects of organic effluents from a salmon farm on a fjord system. III. Linking deposition rates of organic matter and benthic productivity. Aquaculture, 282 (1), 47-53.
    49. Le Moal, Y., 1980. Ecological survey of an intertidal settlement living on a soft substrata in the Aber Benoit and Aber Wrac'h estuaries, after the Amoco Cadiz oil spill. Universite de Bretagne Occidentale, Brest (France), 25pp.
    50. Leppäkoski, E. & Lindström, L., 1978. Recovery of benthic macrofauna from chronic pollution in the sea area off a refinery plant, southwest Finland. Journal of the Fisheries Board of Canada, 35 (5), 766-775.

    51. Leppäkoski, E., 1975. Assessment of degree of pollution on the basis of macrozoobenthos in marine and brackish water environments. Acta Academiae Åboensis, Series B, 35, 1-90.
    52. Linke, O., 1939. Die Biota des Jadebusenwatts. Helgolander Wissenschaftliche Meeresuntersuchungen, 1, 201-348.
    53. Méndez, N., 2006. Effects of teflubenzuron on sediment processing by members of the Capitella species-complex. Environmental Pollution, 139 (1), 118-124.
    54. Mangum, C. & Van Winkle, W., 1973. Responses of aquatic invertebrates to declining oxygen conditions. American Zoologist, 13 (2), 529-541.
    55. McCall, P.L., 1977. Community patterns and adaptive strategies of the infaunal benthos of Long Island Sound. Journal of Marine Research, 35, 221-266.
    56. McLusky, D.S., Teare, M. & Phizachlea, P., 1980. Effects of domestic and industrial pollution on distribution and abundance of aquatic oligochaetes in the Forth estuary. Helgolander Wissenschaftliche Meeresuntersuchungen, 33, 384-392.
    57. Mendez, N., Romero, J. & Flos, J., 1997. Population dynamics and production of the polychaete Capitella capitata in the littoral zone of Barcelona (Spain, NW Mediterranean). Journal of Experimental Marine Biology and Ecology, 218, 263-284.
    58. Mitchell, I.M., 2006. In situ biodeposition rates of Pacific oysters (Crassostrea gigas) on a marine farm in Southern Tasmania (Australia). Aquaculture, 257 (1), 194-203.
    59. Moore, J., 1991. Studies on the Impact of Hydraulic Cockle Dredging on Intertidal Sediment Flat Communities. A report to the Nature Conservancy Council from the Field Studies Council Research Centre, Pembroke, Wales, FSC/RC/4/91.
    60. Nugues, M., Kaiser, M., Spencer, B. & Edwards, D., 1996. Benthic community changes associated with intertidal oyster cultivation. Aquaculture Research, 27 (12), 913-924.
    61. Olsgard, F., 1999. Effects of copper contamination on recolonisation of subtidal marine soft sediments - an experimental field study. Marine Pollution Bulletin, 38, 448-462.
    62. Parr, W., Clarke, S.J., Van Dijk, P., Morgan, N., 1998. Turbidity in English and Welsh tidal waters. Report No. CO 4301/1 to English Nature.

    63. Pearson, T.H. & Rosenberg, R., 1978. Macrobenthic succession in relation to organic enrichment and pollution of the marine environment. Oceanography and Marine Biology: an Annual Review, 16, 229-311.
    64. Peterson, C.H., 1977. Competitive organisation of the soft bottom macrobenthic communities of southern California lagoons. Marine Biology, 43, 343-359.
    65. Petrich, S.M. & Reish, D.J., 1979. Effects of aluminium and nickel on survival and reproduction in polychaetous annelids. Bulletin of Environmental Contamination and Toxicology, 23, 698-702.
    66. Planas, M. & Mora, J., 1989. Epigenetical changes in Capitella (Polychaeta, Capitellidae) in the Ensenada de Lourizan (NW Spain). Vie et Milieu, 39, 159-163.
    67. Qian, P.Y. & Chia, F.S., 1994. In situ measurement of recruitment, mortality, growth, and fecundity of Capitella sp. (Annelida: Polychaeta). Marine Ecology Progress Series, 111, 53-62.
    68. Rabaut, M., Braeckman, U., Hendrickx, F., Vincx, M. & Degraer, S., 2008. Experimental beam-trawling in Lanice conchilega reefs: Impact on the associated fauna. Fisheries Research, 90 (1), 209-216.
    69. Ragnarsson, S.Á. & Raffaelli, D., 1999. Effects of the mussel Mytilus edulis L. on the invertebrate fauna of sediments. Journal of Experimental Marine Biology and Ecology, 241 (1), 31-43.
    70. Redman, C.M., 1985. Effect of temperature and salinity on the life history of Capitella capitata (type I). Dissertation Abstracts, 46, 91.
    71. Rosenberg, R., 1972. Benthic faunal recovery in a Swedish fjord following the closure of a sulphite pulp mill. Oikos, 23, 92-108.
    72. Rostron, D., 1995. The effects of mechanised cockle harvesting on the invertebrate fauna of Llanrhidian sands. In Burry Inlet and Loughor Estuary Symposium, pp. 111-117.
    73. Rygg, B., 1985. Effect of sediment copper on benthic fauna. Marine Ecology Progress Series, 25, 83-89.
    74. Shull, D.H., 1997. Mechanisms of infaunal polychaete dispersal and colonisation in an intertidal sandflat. Journal of Marine Research, 55, 153-179.
    75. Silva, A.C.F., Tavares, P., Shapouri, M., Stigter, T.Y., Monteiro, J.P., Machado, M., Cancela da Fonseca, L. & Ribeiro, L., 2012. Estuarine biodiversity as an indicator of groundwater discharge. Estuarine Coastal and Shelf Science, 97, 38-43.

    76. Soemodinoto, A., Oey, B.L. & Ibkar-Kramadibrata, H., 1995. Effect of salinity decline on macrozoobenthos community of Cibeurum River estuary, Java, Indonesia. Indian Journal of Marine Sciences, 24, 62-67.
    77. Sornin, J.-M., Feuillet, M., Heral, M. & Deslous-Paoli, J.-M., 1983. Effet des biodépôts de l'huître Crassostrea gigas (Thunberg) sur l'accumulation de matières organiques dans les parcs du bassin de Marennes-Oléron. Journal of Molluscan Studies, 49 (supp12A), 185-197.
    78. Suchanek, T.H., 1993. Oil impacts on marine invertebrate populations and communities. American Zoologist, 33, 510-523.
    79. Tait, R.V. & Dipper, R.A., 1998. Elements of Marine Ecology. Reed Elsevier.
    80. Tenore, K.R., 1977. Growth of Capitella capitata cultured on various levels of detritus derived from different sources. Limnology and Oceanography, 22 (5), 936-941.
    81. Tenore, K.R. & Chesney, E.J., 1985. The effects of interaction of rate of food supply and population density on the bioenergetics of the opportunistic polychaete, Capitella capitata (type 1). Limnology and Oceanography, 30 (6), 1188-1195.
    82. Thom, R.M. & Chew, K.K., 1979. The response of subtidal infaunal communities to a change in wastewater discharge. In: Urban Stormwater and Combined Sewers Overflow Impact on Receiving Water Bodies, Orlando, Florida, November 26-28, pp. 174-191.
    83. Van den Broek, W., 1978. Dietary habits of fish populations in the Lower Medway Estuary. Journal of Fish Biology, 13 (5), 645-654.

    84. Van Hoey, G., Guilini, K., Rabaut, M., Vincx, M. & Degraer, S., 2008. Ecological implications of the presence of the tube-building polychaete Lanice conchilega on soft-bottom benthic ecosystems. Marine Biology, 154 (6), 1009-1019.

    85. Ward, T.J. & Young, P.C., 1982. Effects of sediment trace metals and particle size on the community structure of epibenthic seagrass fauna near a lead smelter, South Australia. Marine Ecology Progress Series, 9, 136-146.
    86. Ward, T.J., & Young, P.C., 1983. The depauperation of epifauna on Pinna bicolor near of lead smelter, Spencer Gulf, South Australia Environmental Pollution (Series A), 30, 293-308.
    87. Warren, L.M., 1976. A population study of the polychaete Capitella capitata at Plymouth. Marine Biology, 38, 209-216.
    88. Warren, L.M., 1977. The ecology of Capitella capitata in British waters. Journal of the Marine Biological Association of the United Kingdom, 57, 151-159.
    89. Whomersley, P., Huxham, M., Bolam, S., Schratzberger, M., Augley, J. & Ridland, D., 2010. Response of intertidal macrofauna to multiple disturbance types and intensities – an experimental approach. Marine Environmental Research, 69 (5), 297-308.

    90. Wu, B., Qian, P. & Zhang, S., 1988. Morphology, reproduction, ecology and isoenzyme electrophoresis of Capitella complex in Qingdao. Acta Oceanologica Sinica, 7 (3), 442-458.

    91. Zuhlke, R. & Reise, K., 1994. Response of macrofauna to drifting tidal sediments. Helgolander Meeresuntersuchungen, 48 (2-3), 277-289.

    Citation

    This review can be cited as:

    Tillin, H.M. 2016. Capitella capitata in enriched sublittoral muddy sediments. In Tyler-Walters H. and Hiscock K. (eds) Marine Life Information Network: Biology and Sensitivity Key Information Reviews, [on-line]. Plymouth: Marine Biological Association of the United Kingdom. Available from: http://www.marlin.ac.uk/habitat/detail/106

    Last Updated: 01/06/2016