|Researched by||Georgina Budd||Refereed by||Prof. Jean-Claude Dauvin|
|Authority||(W. Wood, 1802)|
|Other common names||A bivalve mollusc||Synonyms||-|
A bivalve with a brittle shell that may grow up to 2.5 cm in length. The shell is roughly oval in outline, with a slight elongation to the right. Abra alba is white in colour with a glossy shell. The exterior surface of the valves is sculpted with fine concentric lines and growth stages are conspicuous within the overall pattern. The interior of the shell is also white. The periostracum (a flaky epidermis) if present, is light brown in colour.
Widespread around the British Isles.
Abra alba is distributed from the Norwegian Sea and the Baltic, south to the Iberian Peninsula, into the Mediterranean and Black Seas, and south along the coast of Africa to Senegal.
Abra alba is a characteristic inhabitant of inshore muddy fine sand or mud substrates and may be found from the extreme low water-mark offshore to a depth of about 70 m. It is often particularly abundant at around 20 m depth (Tebble, 1976).
- none -
|Phylum||Mollusca||Snails, slugs, mussels, cockles, clams & squid|
|Class||Bivalvia||Clams, cockles, mussels, oysters, and scallops|
|Authority||(W. Wood, 1802)|
|Typical abundance||High density|
|Male size range||< 25mm|
|Male size at maturity||7-9mm|
|Female size range||7-9mm|
|Female size at maturity|
|Body flexibility||None (less than 10 degrees)|
|Characteristic feeding method||Active suspension feeder, Surface deposit feeder|
|Typically feeds on||Phytoplankton, detritus.|
|Is the species harmful?||No|
Although described as solitary animals, adult densities may exceed 1,000 m² in favourable conditions. For instance, in the rich organic muddy harbour sediments in the Ria de la Coruna (NW Spain) Abra alba densities varied from 97 to 2,939 individuals/ m² (Francesch & Lopez-Jamar, 1991). In front of Dunkirk, France, densities can reach 9,000 individuals / m² (Ghertsos et al., 2000). However, abundances typically fluctuate between years owing to variation in recruitment success (juvenile bivalves experience high mortality within the first month after settlement) or adult mortality. High densities of newly settled spat have been reported. For instance, estimated densities of between 16,000 - 22,000 individuals/ m² (collected on 1 mm sieves) were recorded by Jensen (1988) at the time of settlement in the western part of the Limfjord, Denmark.
The smallest recorded benthic specimen had a shell length of 0.34 mm (Dauvin & Gentil, 1989). In autumn settled spat growth is insignificant until spring when a maximum growth rate of 0.1 mm/day was reported (Dauvin, 1986). This growth rate applies from spring to autumn (Dauvin, pers. comm.).
Some bivalves, such as Abra alba, which inhabit muddy low energy environments can switch back and forth from suspension feeding and deposit feeding, depending upon the conditions of the environment (Dame, 1996). While suspension feeding, the inhalant siphon is held a few millimetres above the sediment surface and sucks in suspended particles. For instance, Abra alba significantly reduced the concentration of the flagellate Isochrysis galbana in suspension. Consumption of Isochrysis galbana over four hours was estimated to be 2.7% of the body weight (Rosenberg, 1993). While deposit feeding, the inhalant siphon is bent over toward the sediment surface, sucking up detritus. However, as the food quality of sediments is often low, deposit feeders either have to process large volumes of sediment through the digestive tract in order to gain a small amount of nutrition, or they sort particles before ingestion and reject the majority of particles as pseudofaeces. As a result the feeding rate is lower with a longer residence time for food in the gut, enabling digestion of the more complex organic compounds common to the benthic environment (Dame, 1996).
Biomass and productivity
In Kiel Bay, mean annual biomass varied greatly between sites and between years: Biomass (B) =0.1-3 g AFDW m², with a long-term average (ratio) P:B = c 2.2 (Rainer, 1985); B = 0.1-2 g AFDW m² and P:B = 1.7-2.9 from five years of sampling at a location off the French coast (Dauvin, 1986); B = 0.3 g AFDW m² and P:B = 1.4 in the Bristol Channel, England (Warwick & George, 1980).
|Physiographic preferences||Open coast, Offshore seabed, Strait / sound, Sea loch / Sea lough, Enclosed coast / Embayment|
|Biological zone preferences||Lower circalittoral, Lower infralittoral, Sublittoral fringe, Upper circalittoral, Upper infralittoral|
|Substratum / habitat preferences||Mud, Muddy gravel, Muddy sand, Sandy mud|
|Tidal strength preferences||Weak < 1 knot (<0.5 m/sec.)|
|Wave exposure preferences||Sheltered|
|Salinity preferences||Full (30-40 psu)|
|Depth range||Lower shore to 70 m depth|
No text entered
|Migration Pattern||Non-migratory / resident|
Dispersal of post-larval bivalve molluscs
The mechanism termed 'byssus drifting' has been observed in 20 species of bivalve molluscs, including Abra alba, and is the mechanism by which post-larval bivalves enter a second pelagic migratory stage. Young bivalves secrete a single, long thread which increases the drag acting upon them and enables them to be carried along on the current. The drag increase was found to be a factor of 3 to 30 times greater on byssus secreting bivalves than on inactive ones (Sigurdsson et al., 1976). Abra alba were observed to re-enter the water column after larval settlement in the Bay of Seine (Olivier et al., 1996). The post-larvae and juveniles of Abra alba were most abundant at flood tide velocities . Furthermore, Abra alba were found to vary significantly in their vertical distribution in the water column, the species decreasing in abundance with distance from the sea bed. It was noted that Abra alba juveniles can regulate their vertical position in the flow, to some extent, by opening their valves to different extents (Olivier et al., 1996).
|Reproductive type||Gonochoristic (dioecious)|
|Reproductive frequency||Annual protracted|
|Fecundity (number of eggs)||10,000-100,000|
|Generation time||See additional information|
|Age at maturity||See additional information|
|Season||February - Autumn|
|Life span||See additional information|
|Duration of larval stage||1-2 months|
|Larval dispersal potential||Greater than 10 km|
|Larval settlement period||Insufficient information|
The MarLIN sensitivity assessment approach used below has been superseded by the MarESA (Marine Evidence-based Sensitivity Assessment) approach (see menu). The MarLIN approach was used for assessments from 1999-2010. The MarESA approach reflects the recent conservation imperatives and terminology and is used for sensitivity assessments from 2014 onwards.
|Abra alba lives infaunally in muddy sediments. Removal of the substratum would also remove the entire population of the species and so intolerance has been assessed to be high. Recoverability has been assessed to be high (see additional information below).|
|Abra alba is a shallow burrower in muddy sediments. It requires its inhalant siphon to be above the sediment surface for feeding and respiration. Sudden smothering with 5 cm of sediment would temporarily halt feeding and respiration and require the species to relocate to its preferred depth. As an active burrower Abra alba would be expected to relocate with no mortality. However, growth and reproduction may be compromised owing to energetic expenditure and so intolerance has been assessed to be low. Growth and reproduction would return to normal following relocation so recoverability is recorded as immediate.|
|Tolerant*||Not relevant||Not sensitive*||Moderate|
|Levels of suspended sediment are likely to be most relevant to feeding. Abra alba practices two alternative modes of feeding. It either holds its feeding organ, the inhalant siphon, at a fixed position just above the sediment surface to filter out food particles suspended in the overlying water or else extends and moves its siphon around on the sediment above it to vacuum up deposited food particles. The alternative feeding methods are likely to make the species insensitive to relatively small changes in suspended sediment. If the level of suspended sediment becomes so high as to risk clogging the feeding structures, Abra alba could presumably switch to deposit feeding. Furthermore, an increase in suspended sediment is likely to increase the rate of siltation and therefore the food available to deposit feeders. Abra alba has been assessed to be tolerant at the benchmark level increase of 100 mg/ l for one month, with the potential for growth and reproduction to be enhanced by the increased food supply. However, a more substantial increase in suspended sediment levels would be expected to have a detrimental effect. For instance, the abundance of Abra alba declined over two years in the 1 km vicinity of an outfall pipe discharging fine-grained mineral waste from the china clay industry at a rate of 450, 000 tons per year to Mevagissey Bay, Cornwall. However, it was argued that persistent sediment instability was the more significant source of stress to the predominantly deposit-feeding community than the suspended sediment concentration (Probert, 1981).|
|Abra alba practices two alternative modes of feeding. It either holds its feeding organ, the inhalant siphon, at a fixed position just above the sediment surface to filter out food particles suspended in the overlying water or else extends and moves its siphon around on the sediment above it to vacuum up deposited food particles. A decrease in suspended sediment is likely to decrease the availability of food for both suspension and deposit feeding. The reduction in food availability may result in less energy available for growth and reproduction by Abra alba. However, the benchmark change period is one month, during which time it is not expected that mortality would occur and so intolerance is assessed as low. When suspended sediment returns to original levels, growth and reproduction should quickly return to normal so recoverability has been assessed to be immediate.|
|Abra alba lives infaunally in muddy sediments (Tebble, 1976) and is therefore likely to be largely protected from desiccation stress by its environmental position. Additionally, bivalves are able to respond to desiccation stress by valve adduction during periods of emersion. It is likely that Abra alba would be able to retain enough water within its shell to avoid mortality during the benchmark emersion period of one hour. However, during the period of emersion, the species would not be able to feed and respiration would be compromised, so there is likely to be some energetic cost. Intolerance has been assessed to be low. On immersion, metabolic activity should quickly return to normal and recoverability has been assessed to be immediate.|
|Although a largely subtidal species, a proportion of the population of Abra alba occurs in the proximity of the sublittoral fringe and so may be vulnerable to an increase in the emergence regime. The species does not colonize further up the shore and therefore must be limited by one or more factors including desiccation, temperature and wave exposure. An increase in the emergence regime may suppress the upper distribution of the population, some individuals may die and intolerance has been assessed to be intermediate. On return to prior conditions recolonization is likely and recoverability has been assessed to be very high (see additional information below).|
|Tolerant||Not relevant||Not sensitive||High|
|Abra alba occurs in the subtidal zone and could therefore benefit from a decrease in the emergence regime.|
|Low||Very high||Very Low||Low|
|Abra alba lives in low energy environments (Tebble, 1976) where the substratum has a high proportion of fine sediment. Increased water flow rate will change the sediment characteristics in which the species lives, primarily by winnowing away the surface layers and preventing deposition of finer particles (Hiscock, 1983). Furthermore, increased water flow rate may prevent settlement of larvae and therefore reduce recruitment. Mature adults buried at depth are likely to be unaffected as muddy substrata is particularly cohesive. An intolerance assessment of low has been made owing to reduced viability that may result from poor larval recruitment. Recoverability has been assessed to be very high as the adult population is likely to have survived (see additional information below).|
|Low||Very high||Very Low||Low|
|Abra alba occurs in areas of weak water flow rate, so the benchmark decrease in water flow rate will expose the species to conditions of almost negligible flow. Decreased water flow may reduce the availability of food that may be obtained from suspension feeding and the species would have to switch to deposit feeding. A decreased water flow rate may favour the deposition of material upon which Abra alba could feed. However, a decreased water flow rate may mean that dispersion of planktonic larvae is minimal, and that recruitment to the benthos occurs in the vicinity of the parent population which may result in parent induced mortality (via feeding). Intolerance has therefore been assessed to be low and recoverability assessed to be very high (see additional information below).|
|Low||Very high||Very Low||Moderate|
|Abra alba has a wide geographic range, occurring in waters to the south of the British Isles. It is likely therefore to be tolerant of higher temperatures than it experiences in Britain and Ireland. No specific information concerning temperature tolerances of Abra alba was found, but inferences of the effects may be made from other species of bivalve. For instance, Wilson (1978) reported the 24 hour LT50 for Fabulina fabula (studied as Tellina fabula) from Millport in Scotland to be 26.5 °C and noted that acclimation to higher temperatures enhanced the species' ability to withstand higher experimental temperatures. Similarly, Ansell et al. (1980) reported the 24 hour LT50 for Fabulina fabula (studied as Tellina fabula and acclimated at 10 °C) from Millport to be 27 °C. The 96 hour LT50 was 24-27 °C depending on acclimation temperature. Growth experiments by Salzwedel (1979) revealed that growth of Fabulina fabula (studied as Tellina fabula) correlated positively with temperature up to about 16 °C after which temperature increase inhibited growth. Considering that maximum sea surface temperatures around the British Isles rarely exceed 20 °C (Hiscock, 1998), it is unlikely that Abra alba would suffer mortality due to the benchmark increase in temperature. However, elevated temperatures would probably result in inhibition of growth and hence intolerance has been assessed to be low. A normal growth rate would resume on return to prior conditions so recoverability has been assessed to be very high.|
|Abra alba has a wide geographic range, occurring in waters to the north of the British Isles. It is likely therefore to be tolerant of lower temperatures than it experiences in Britain and Ireland and would probably tolerate a long term chronic decrease of 2 °C. However, a short term acute periods of extreme cold and icing conditions are likely to cause stress and some mortality in bivalve populations (Dame, 1996). For instance, during the 1978/79 winter which was very cold with severe ice conditions, water temperature in the outer Weser estuary, Germany, remained below 0 °C on 45 successive days. Characteristic species of the benthos, including Abra alba were considerably damaged (Buhr, 1981). The intolerance of Abra alba to a short-term acute decrease in temperature has been assessed to be intermediate as a substantial proportion of the population maybe killed. The species is likely to re-populate and recovery has been assessed to be very high (see additional information below).|
|Low||Very high||Very Low||Low|
|Abra alba does not require light and therefore the effects of increased turbidity on light attenuation are not directly relevant. An increase in turbidity may affect primary production in the water column and therefore reduce the availability of phytoplankton food. However, phytoplankton will also be transported from distant areas and so the effect of increased turbidity may be mitigated to some extent. The increased turbidity only persists for a year, so decreased food availability would probably only affect growth and fecundity and an intolerance of low has been recorded. As soon as light levels return to normal, primary production will increase, the species would resume optimal feeding, so recoverability has been assessed to be very high (see additional information below).|
|Tolerant||Not relevant||Not sensitive||Low|
|Abra alba does not require light and therefore the effects of decreased turbidity on light attenuation are not directly relevant. It is possible that decreased turbidity would increase primary production in the water column by phytoplankton and by microphytobenthos. The resultant increase in food availability may enhance growth and reproduction in Abra alba, but only if food was previously limiting.|
|An increase in wave exposure of two categories for one year would place the majority of the population in areas frequently subject to strong wave action and the species may be affected in several ways. Strong wave action may cause damage or withdrawal of the siphons, resulting in loss of feeding opportunities and compromised growth. Furthermore, individuals may be dislodged by scouring from sand and gravel mobilised by increased wave action. During winter gales along the North Wales coast, large numbers of Abra alba were cast ashore and over winter survival rate was as low as 7% in the more exposed locations (Rees et al., 1977). Olivier et al. (1996) reported that the post-larvae and juveniles of Abra alba were most abundant in the near-bottom water stratum at flood tides. Therefore, increased wave action could result in enhanced resuspension and dispersal of early life stages. Overall, some mortality would be likely to occur and intolerance is recorded as intermediate. Recoverability has been assessed to be very high (see additional information below).|
|Tolerant||Not relevant||Not sensitive||Low|
|Olivier et al. (1996) reported that the post-larvae and juveniles of Abra alba were most abundant in the near-bottom water stratum at flood tide velocities. Therefore, a reduction in wave exposure may lead to a decrease in dispersal of Abra alba. Changes in wave exposure are likely to have marked effects on the sediment dynamics of the shore. Decreased exposure will probably lead to increased siltation and reduced grain size (muddy sediment). However, as Abra alba favours muddy substrata such a change in the substratum in unlikely to affect the species and, overall, it has been assessed tolerant.|
|Tolerant||Not relevant||Not sensitive||Moderate|
|No information was found concerning the intolerance of Abra alba to noise. The siphons are likely to detect vibrations and are probably withdrawn as a predator avoidance mechanism, but the species is not expected to be sensitive at the level of the benchmark.|
|Not relevant||Not relevant||Not relevant||Not relevant|
|Abra alba does not have visual acuity and an intolerance assessment for this factor was not considered to be relevant.|
|Despite their robust body form, bivalves are vulnerable to physical abrasion. For example, as a result of dredging activity, mortality and shell damage has been reported in Mya arenaria and Cerastoderma edule (Cotter et al., 1997). Abra alba is a shallow burrower and has a fragile shell (Tebble, 1976) and may be damaged by impact Bergmann & Santbrink (2000) reported between <0.5%and 18% mortality of Abra alba due to trawling in the southern North Sea, depending on the type of trawl (12 m or 6 m beam trawl or otter trawl). They included Abra alba amongst their list of bivalve species most vulnerable to trawling. However, they noted that many bivalve species were able to maintain a population in the face of fishing effort, depending on their life history characteristics. Therefore, intolerance has been assessed to be intermediate. Recoverability has been assessed to be very high (see additional information below).|
|Abra alba probably burrows into the sediment within a few minutes when displaced to the surface of muddy substrata. The species is therefore probably relatively tolerant of displacement. However, exposure at the sediment surface would increase the risk of predation, for example by the starfish Asterias rubens and flatfish predators (Allen, 1983; Rainer, 1985; Basimi & Grove, 1985), so intolerance has been assessed to be intermediate. Recoverability for the majority of individuals has been assessed to be immediate.|
|Abra alba demonstrated alterations of its behaviour in response to exposure to marine sediments contaminated with pesticides (6000 ppm parathion, 200 ppm methyl parathion, 200 ppm malathion). No burrowing occurred in the most contaminated sediment, whilst burrowing was impaired in the moderately contaminated sediment with a median effective burrowing time (ET(50)) of 9.0 (±3.0 - 28) minutes in comparison to a control time of 4.5 (±2.8 - 7.2) minutes (Møhlenberg & Kiørboe, 1983). Impaired burrowing would result in the species being exposed to predatory starfish and fish. However, no other information was found concerning the effects of synthetic chemicals specifically on Abra alba. However, inference can be drawn from related species. Beaumont et al. (1989) concluded that bivalves are particularly sensitive to tri-butyl tin (TBT), the toxic component of many antifouling paints. For example, when exposed to 1-3 µg TBT/l, Cerastoderma edule and Scobicularia plana suffered 100% mortality after 2 weeks and 10 weeks respectively. There is also evidence that TBT causes recruitment failure in bivalves, either due to reproductive failure or larval mortality (Bryan & Gibbs, 1991). Stirling (1975) investigated the effects of phenol, a non-persistent, semi-synthetic organic pollutant, on Tellina tenuis. Exposure to phenol produced a measurable effect on burrowing at all concentrations tested, i.e. 50 mg/l and stronger. Sub-lethal effects of exposure to phenol included delayed burrowing and valve adduction to exclude the pollutant from the mantle cavity. After exposure to 100 mg/l for 24 hours, the majority of animals were extended from their shells and unresponsive to tactile stimulation. Following replacement of the phenol solution with clean seawater, good recovery was exhibited after 2 days for animals exposed to 50 mg/l and some recovery occurred after 4 days for animals exposed to 100 mg/l. In light of the intolerance of other bivalve species, intolerance of Abra alba to synthetic chemicals has been assessed to be high. Recoverability has been assessed to be high (see additional information below) but would be partially dependent on the persistence time of synthetic contaminants in the sediments.|
|Abra alba can live in polluted sediments (Dauvin, pers. comm.), for example, near Calais where high densities of Abra alba were found in sediment containing 8mg/g iron and 4 mg/g titanium (Dewarumez et al, 1976). The capacity of bivalves to accumulate heavy metals in their tissues, far in excess of environmental levels, is well known. Reactions to sub-lethal levels of heavy metals include siphon retraction, valve closure, inhibition of byssal thread production, disruption of burrowing behaviour, inhibition of respiration, inhibition of filtration rate, inhibition of protein synthesis and suppressed growth (see review by Aberkali & Trueman, 1985). Bryan (1984) states that Hg is the most toxic metal to bivalve molluscs while Cu, Cd and Zn seem to be most problematic in the field. In bivalve molluscs Hg was reported to have the highest toxicity, mortalities occurring above 0.1-1 g/l after 4-14 days exposure (Crompton, 1997), toxicity decreasing from Hg > Cu and Cd > Zn > Pb and As > Cr ( in bivalve larvae, Hg and Cu > Zn > Cd, Pb, As, and Ni > to Cr). Owing to evidence in the literature of sub-lethal effects and mortality of bivalves, intolerance of Abra alba to heavy metal contamination has been assessed to be intermediate. Recoverability is recorded as high (see additional information below) but would be partially dependent on the persistence time of heavy metals in the sediments.|
|Low||Very high||Very Low||High|
|Suchanek (1993) reviewed the effects of oil on bivalves. Sublethal concentrations may produce substantially reduced feeding rates and/or food detection ability, probably due to ciliary inhibition. Respiration rates may increase at low concentrations and decrease at high concentrations. Generally, contact with oil causes an increase in energy expenditure and a decrease in feeding rate, resulting in less energy available for growth and reproduction. However, the Abra alba population affected by the 1978 Amoco Cadiz benefited from the nutrient enrichment caused by the oil pollution (see nutrient enrichment, below). The biomass of the fine-sand community remained low in 1979, a year after the spill, owing to the decimation of the Ampelisca amphipod population, but the biomass then doubled as a result of an increase in Abra alba abundance in 1980 and Abra alba remained a dominant species over the 20 year duration over which recovery of the community was monitored (Dauvin, 1998). Intolerance has been assessed to be low as the Abra alba population was apparently resilient to the presence of hydrocarbons in the subtidal sediments just two weeks after the wreck. The fact that Abra alba occurs subtidally may mitigate the effects of oil pollution on the species, as it avoids a direct oiling. Recoverability has been assessed to be very high as the species is able to adapt its demographic strategy in order to benefit from the resulting nutrient enrichment (Dauvin & Gentil, 1989).|
|No information||Not relevant||No information||Not relevant|
|No information was found concerning the effects of radionuclide contamination on Abra alba.|
|Tolerant*||Not relevant||Not sensitive*||High|
|In a sewage dumping region of the North Sea, a great increase in the abundance of Abra alba occurred in much of the dumping area because of the ecological adaptations of the species enabled it to exploit the greatly increased supply of nutrients (Caspers, 1981). For example, the Amoco Cadiz oil spill in March 1978 caused vast disturbance to the fine-sand communities of the Bay of Morlaix, France (Dauvin, 1982). Drastic qualitative and quantitative changes in species abundance, diversity and biomass were recorded after the spill. However, the Abra alba population persisted in the disturbed environment under eutrophic conditions and as an 'opportunistic species' (Hily & Le Bris, 1984), it rapidly adapted its reproductive strategy by increasing its reproductive output to three spawnings per year. Increased growth and abundance was attributable to increased food availability and vacant ecological niches (Dauvin & Gentil, 1989). As Abra alba was able to adapt its demographic strategy in order to benefit from the nutrient enrichment, it has been assessed to be tolerant*.|
|Not relevant||Not relevant||Not relevant||Low|
|Abra alba is typically found in full salinity conditions. No information was found concerning the effects of hypersaline conditions on Abra alba.|
|Abra alba is typically found in full salinity conditions and is therefore likely to be intolerant of reductions in salinity in some way. The benchmark decrease in salinity would place the population in areas of variable salinity for one year or reduced salinity for one week. The change would be likely to cause inhibition of growth and reproduction and exposure to low salinity may result in some mortality. Intolerance has been assessed to be intermediate. Recoverability has been assessed to be very high as a proportion of the adult population are likely to remain.|
|Tolerant||Not relevant||Not sensitive||High|
|Abra alba is typically found in organically enriched sediments where it may be present in high densities (Dauvin & Gentil, 1989). Such areas can be prone to periodic oxygen deficiency and individual growth and survival is dependent upon the maintenance of a continuous balance between high energy input (food availability) and high metabolic costs which result from periodic anaerobic metabolism and regulation of oxygen uptake (Hylland et al., 1996). Experimental examination of the interactions between eutrophication and oxygen deficiency (2.4 - 3.5 mg O2/ l over a 93 day experimental period) revealed that Abra alba became inefficient in its use of the available organic matter under prolonged conditions of hypoxia, as evidenced by a decreased growth rate (Hylland et al., 1996). However, the benchmark assesses species' intolerance to hypoxia for one week and as Abra alba is able to shift from aerobic to anaerobic respiration, a short period of hypoxia is unlikely to have a significant effect upon the species and Abra alba has been assessed to be not sensitive at the benchmark level. However, prolonged exposure to oxygen concentrations below 3 mg O2/ l may severely decrease growth and survival (Hylland et al., 1996) and intolerance would be expected to be higher.|
|No information||Not relevant||No information||Not relevant|
|More than 20 viruses have been described for marine bivalves (Sinderman, 1990). Bacterial diseases are more significant in the larval stages and protozoans are the most common cause of epizootic outbreaks that may result in mass mortalities of bivalve populations. Parasitic worms, trematodes, cestodes and nematodes can reduce growth and fecundity within bivalves and may in some instances cause death (Dame, 1996). However, no information specifically concerning the effects of microbial pathogens and parasites on the viability of Abra alba was found.|
|Not relevant||Not relevant||Not relevant||Not relevant|
|No evidence was found concerning the effect of non-native species on the viability of Abra alba.|
|Not relevant||Not relevant||Not relevant||Not relevant|
|Abra alba is not a species targeted for extraction.|
|Dredging for scallops and use of other mobile fishing gear may cause abrasion and displacement of Abra alba. The delicate shell are vulnerable to physical damage (e.g. by otter boards; Rumohr & Krost, 1991), but the small size of Abra alba relative to meshes of commercial trawls may ensure survival of at least a moderate proportion of disturbed individuals which pass through (Rees & Dare, 1993). Intolerance has been assessed to be intermediate and recoverability very high (see additional information below).|
- no data -
|National (GB) importance||-||Global red list (IUCN) category||-|
Aberkali, H.B. & Trueman, E.R., 1985. Effects of environmental stress on marine bivalve molluscs. Advances in Marine Biology, 22, 101-198.
Allen, P.L. 1983. Feeding behaviour of Asterias rubens (L.) on soft bottom bivalves: a study in selective predation. Journal of Experimental Marine Biology and Ecology, 70, 79-90.
Basimi, R.A. & Grove, D.J., 1985. Estimates of daily food intake by an inshore population of Pleuronectes platessa L. off eastern Anglesey, north Wales. Journal of Fish Biology, 27, 505-520.
Beaumont, A.R., Newman, P.B., Mills, D.K., Waldock, M.J., Miller, D. & Waite, M.E., 1989. Sandy-substrate microcosm studies on tributyl tin (TBT) toxicity to marine organisms. Scientia Marina, 53, 737-743.
Bergman, M.J.N. & Van Santbrink, J.W., 2000b. Fishing mortality of populations of megafauna in sandy sediments. In The effects of fishing on non-target species and habitats (ed. M.J. Kaiser & S.J de Groot), 49-68. Oxford: Blackwell Science.
Bryan, G.W. & Gibbs, P.E., 1991. Impact of low concentrations of tributyltin (TBT) on marine organisms: a review. In: Metal ecotoxicology: concepts and applications (ed. M.C. Newman & A.W. McIntosh), pp. 323-361. Boston: Lewis Publishers Inc.
Bryan, G.W., 1984. Pollution due to heavy metals and their compounds. In Marine Ecology: A Comprehensive, Integrated Treatise on Life in the Oceans and Coastal Waters, vol. 5. Ocean Management, part 3, (ed. O. Kinne), pp.1289-1431. New York: John Wiley & Sons.
Buhr, K.-J., 1981. Effects of the cold winter 1978/79 on the macrobenthos of the Lanice-association in the Weser Estuary. Veroffentlichungen des Instituts fur Meeresforschung in Bremerhaven, 19, 115-131.
Caspers, H., 1981. Long-term changes in benthic fauna resulting from sewage sludge dumping in the North Sea. Water Science and Technology, 13, 461-479.
Cotter, A.J.R., Walker, P., Coates, P., Cook, W. & Dare, P.J., 1997. Trial of a tractor dredger for cockles in Burry Inlet, South Wales. ICES Journal of Marine Science, 54, 72-83.
Crisp, D.J. (ed.), 1964. The effects of the severe winter of 1962-63 on marine life in Britain. Journal of Animal Ecology, 33, 165-210.
Crompton, T.R., 1997. Toxicants in the aqueous ecosystem. New York: John Wiley & Sons.
Dame, R.F.D., 1996. Ecology of Marine Bivalves: an Ecosystem Approach. New York: CRC Press Inc. [Marine Science Series.]
Dauvin, J-C. & Gentil, F., 1989. Long-term changes in populations of subtidal bivalves (Abra alba and Abra prismatica) from the Bay of Morlaix (Western English Channel). Marine Biology, 103, 63-73.
Dauvin, J-C., 1988. Rôle du macrobenthos dans l'alimentation des Poissons démersaux sur les fonds de sédiments fins de la Manche occidentale. Cahiers de Biologie Marine, 29, 445-467.
Dauvin, J.-C., 1986. Biologie, dynamique et production d'une population d' Abra alba (Wood) (mollusque-bivalve) de la baie de Morlaix (Manche occidentiale). Journal of Experimental Marine Biology and Ecology, 97, 151-180.
Dauvin, J.C., 1982. Impact of Amoco Cadiz oil spill on the muddy fine sand Abra alba - Melinna palmata community from the Bay of Morlaix. Estuarine and Coastal Shelf Science, 14, 517-531.
Dauvin, J.C., 1998. The fine sand Abra alba community of the Bay of Morlaix twenty years after the Amoco Cadiz oil spill. Marine Pollution Bulletin, 36, 669-676.
Dewarumez, J-M., 1979. Etude biologique d'Abra alba (Wood) Mollusque lamellibranche du littoral français de la mer du Nord. , Thèse de 3ème cycle, Université des Sciences et Techniques de Lille. 139 p, 23 annexes.
Dewarumez, J-M., Smigielski, F. & Richard, A., 1976. Abra alba (mollusque lamellibranche) sa localisation en zone littorale de la mer du Nord. Haliotis, 7, 13-19.
Diaz-Castaneda, V., Richard, A. & Frontier, S., 1989. Preliminary results on colonization, recovery and succession in a polluted areas of the southern North Sea (Dunkerque's Harbour, France). Scientia Marina, 53, 705-716.
Emerson, C.W. & Grant, J., 1991. The control of soft-shell clam (Mya arenaria) recruitment on intertidal sandflats by bedload sediment transport. Limnology and Oceanography, 36, 1288-1300.
Francesch, O. & Lopez-Jamar, E., 1991. Dynamics, growth and production of Abra alba and Abra nitida from La Coruna, NW of Spain. Boletin del Instituto Espanol de Oceanografia, Madrid, 7, 101-113.
Ghertsos, K., Luczak, C., Dewarumez, J-M. & Dauvin, J-C., 2000. Influence of spatial scales of observation on temporal change in diversity and trophic structure of fine-sand communities from the English Channel and the southern North Sea. ICES Journal of Marine Science, 57, 1481-1487.
Hayward, P.J. & Ryland, J.S. (ed.) 1995b. Handbook of the marine fauna of North-West Europe. Oxford: Oxford University Press.
Hily, C. & Le Bris, H., 1984. Dynamics of an Abra alba population (Bivalve: Scrobiculariidae) in the Bay of Brest. Estuarine and Coastal Shelf Science, 19, 463-475.
Howson, C.M. & Picton, B.E., 1997. The species directory of the marine fauna and flora of the British Isles and surrounding seas. Belfast: Ulster Museum. [Ulster Museum publication, no. 276.]
Hylland, K., Sköld, M., Gunnarsson, J.S. & Skei, J., 1996. Interactions between eutrophication and contaminants. IV. Effects on sediment-dwelling organisms. Marine Pollution Bulletin, 33, 90-99.
Jensen, J.N., 1988. Recruitment, growth and mortality of juvenile Corbula gibba and Abra alba in the Limfjord, Denmark. The Baltic Sea environment: history, eutrophication, recruitment and toxicology. Kieler Meeresforschungen (Sonderheft), 6, 357-365.
JNCC (Joint Nature Conservation Committee), 1999. Marine Environment Resource Mapping And Information Database (MERMAID): Marine Nature Conservation Review Survey Database. [on-line] http://www.jncc.gov.uk/mermaid
Møhlenberg, F. & Kiørboe, T., 1983. Burrowing and avoidance behaviour in marine organisms exposed to pesticide-contaminated sediment. Marine Pollution Bulletin, 14 (2), 57-60.
Nott, P.L., 1980. Reproduction in Abra alba (Wood) and Abra tenuis (Montagu) (Tellinacea: Scrobiculariidae) Journal of the Marine Biological Association of the United Kingdom, 60, 465-479.
Olivier, F., Vallet, C., Dauvind, J-C. & Retière, C., 1996. Drifting in post-larvae and juveniles in an Abra alba (Wood) community of the eastern part of the Bay of Seine (English Channel). Journal of Experimental Marine Biology and Ecology, 199, 89-109.
Picton, B.E. & Costello, M.J., 1998. BioMar biotope viewer: a guide to marine habitats, fauna and flora of Britain and Ireland. [CD-ROM] Environmental Sciences Unit, Trinity College, Dublin.
Probert, P.K., 1981. Changes in the benthic community of china clay waste deposits is Mevagissey Bay following a reduction of discharges. Journal of the Marine Biological Association of the United Kingdom, 61, 789-804.
Rainer, S.F., 1985. Population dynamics and production of the bivalve Abra alba and implications for fisheries production. Marine Biology, 85, 253-262.
Rees, E.I.S., Nicholaidou, A. & Laskaridou, P., 1977. The effects of storms on the dynamics of shallow water benthic associations. In Proceedings of the 11th European Symposium on Marine Biology, Galway, Ireland, October 5-11, 1976. Biology of Benthic Organisms, (ed. B.F. Keegan, P. O'Ceidigh & P.J.S. Boaden), pp. 465-474.
Rees, H.L. & Dare, P.J., 1993. Sources of mortality and associated life-cycle traits of selected benthic species: a review. MAFF Fisheries Research Data Report, no. 33., Lowestoft: MAFF Directorate of Fisheries Research.
Rosenberg, R., 1993. Suspension feeding in Abra alba (Mollusca). Sarsia, 78, 119-121.
Sigurdsson, J.B., Titman, C.W. & Davies, P.A., 1976. The dispersal of young post-larval bivalve molluscs by byssus threads. Nature, 262, 386-387.
Sinderman, C.J., 1990. Principle diseases of marine fish and shellfish, 2nd edition, Volume 2. Diseases of marine shellfish. Academic Press, 521 pp.
Stirling, E.A., 1975. Some effects of pollutants on the behaviour of the bivalve Tellina tenuis. Marine Pollution Bulletin, 6, 122-124.
Suchanek, T.H., 1993. Oil impacts on marine invertebrate populations and communities. American Zoologist, 33, 510-523.
Tebble, N., 1976. British Bivalve Seashells. A Handbook for Identification, 2nd ed. Edinburgh: British Museum (Natural History), Her Majesty's Stationary Office.
Warwick, R.M. & George, C.L., 1980. Annual macro-fauna production in an Abra community. In Industrialised embayments and their environmental problems: a case study of Swansea Bay (ed. M.B. Collins et al.), pp. 517-538. Oxford: Pergamon Press.
Centre for Environmental Data and Recording, 2018. Ulster Museum Marine Surveys of Northern Ireland Coastal Waters. Occurrence dataset https://www.nmni.com/CEDaR/CEDaR-Centre-for-Environmental-Data-and-Recording.aspx accessed via NBNAtlas.org on 2018-09-25.
Conchological Society of Great Britain & Ireland, 2017. Mollusc (marine) data for Great Britain and Ireland. Occurrence dataset https://doi.org/10.15468/aurwcz accessed via GBIF.org on 2018-07-24.
Conchological Society of Great Britain & Ireland, 2018. Mollusc (marine) data for Great Britain and Ireland - restricted access. Occurrence dataset: https://doi.org/10.15468/4bsawx accessed via GBIF.org on 2018-09-25.
Conchological Society of Great Britain & Ireland, 2018. Mollusc (marine) data for Great Britain and Ireland. Occurrence dataset: https://doi.org/10.15468/aurwcz accessed via GBIF.org on 2018-09-25.
Environmental Records Information Centre North East, 2018. ERIC NE Combined dataset to 2017. Occurrence dataset: http://www.ericnortheast.org.uk/home.html accessed via NBNAtlas.org on 2018-09-38
Fife Nature Records Centre, 2018. St Andrews BioBlitz 2014. Occurrence dataset: https://doi.org/10.15468/erweal accessed via GBIF.org on 2018-09-27.
Kent Wildlife Trust, 2018. Biological survey of the intertidal chalk reefs between Folkestone Warren and Kingsdown, Kent 2009-2011. Occurrence dataset: https://www.kentwildlifetrust.org.uk/ accessed via NBNAtlas.org on 2018-10-01.
Kent Wildlife Trust, 2018. Kent Wildlife Trust Shoresearch Intertidal Survey 2004 onwards. Occurrence dataset: https://www.kentwildlifetrust.org.uk/ accessed via NBNAtlas.org on 2018-10-01.
Merseyside BioBank., 2018. Merseyside BioBank (unverified). Occurrence dataset: https://doi.org/10.15468/iou2ld accessed via GBIF.org on 2018-10-01.
NBN (National Biodiversity Network) Atlas. Available from: https://www.nbnatlas.org.
OBIS (Ocean Biogeographic Information System), 2021. Global map of species distribution using gridded data. Available from: Ocean Biogeographic Information System. www.iobis.org. Accessed: 2021-06-17
Outer Hebrides Biological Recording, 2018. Invertebrates (except insects), Outer Hebrides. Occurrence dataset: https://doi.org/10.15468/hpavud accessed via GBIF.org on 2018-10-01.
South East Wales Biodiversity Records Centre, 2018. SEWBReC Molluscs (South East Wales). Occurrence dataset: https://doi.org/10.15468/jos5ga accessed via GBIF.org on 2018-10-02.
Suffolk Biodiversity Information Service., 2017. Suffolk Biodiversity Information Service (SBIS) Dataset. Occurrence dataset: https://doi.org/10.15468/ab4vwo accessed via GBIF.org on 2018-10-02.
This review can be cited as:
Last Updated: 03/07/2007
Tags: Bivalve Mollusc white furrow shell