|Researched by||Dr Keith Hiscock||Refereed by||This information is not refereed.|
|EUNIS Code||A5.528||EUNIS Name||Filamentous green seaweeds on low salinity infralittoral mixed sediment or rock|
|EUNIS 2008||A5.528||Filamentous green seaweeds on low salinity infralittoral mixed sediment or rock|
|EUNIS 2006||A5.528||Filamentous green seaweeds on low salinity infralittoral mixed sediment or rock|
|JNCC 2004||SS.SMp.KSwSS.FilG||Filamentous green seaweeds on low salinity infralittoral mixed sediment or rock|
|1997 Biotope||SS.IMX.KSwMx.FiG||Filamentous green seaweeds on low salinity infralittoral mixed sediment or rock|
Shallow muddy sediments, often with boulders, cobbles and pebbles around the edges of lagoons, or other areas that are exposed to wide salinity variations are unsuitable for colonisation by many species. Such areas may be colonised by a dense blanket of ephemeral green algae such as Enteromorpha spp., Chaetomorpha linum, Cladophora liniformis or Rhizoclonium riparium. This biotope may also contain some red seaweeds, such as Furcellaria lumbricalis, but always at low abundance (compare with PolFur). Amongst the filamentous green algae, grazing molluscs and solitary ascidians may be present. Infauna may typically include Corophium volutator, Heterochaeta costata, Tubificoides benedeni and other taxa suited for low/variable salinity environments (JNCC, 2015).
Recorded in Scottish lagoons and the Isles of Scilly, Cornwall.
|Recorded distribution in Britain and Ireland|
Recorded in Scottish lagoons and the Isles of Scilly, Cornwall.
|Depth Range||0-5 m, 5-10 m|
|Water clarity preferences|
|Limiting Nutrients||Data deficient|
|Salinity||Full (30-40 psu), Variable (18-40 psu)|
|Tidal||Very Weak (negligible), Weak < 1 knot (<0.5 m/sec.)|
|Other preferences||See additional information|
There appear to be three critical habitat characteristics that determine the development of this biotope: extreme shelter from wave action, very variable, reduced or low salinity, and presence of hard and sediment substrata. Low salinity in particular means that the habitat is unsuitable for many species and a few tolerant species thrive. Absence of significant tidal flow is also important.
The characterizing species and other important habitat factors are based on the JNCC (2015) biotope description. This biotope is characterized by shallow muddy sediments, often with boulders, cobbles and pebbles around the edges of lagoons, or other areas that are exposed to wide salinity variations that prevent colonization by many species. This biotope is characterized by ephemeral green algae such as Enteromorpha spp., Chaetomorpha linum, Cladophora liniformis or Rhizoclonium riparium and some red seaweeds, such as Furcellaria lumbricalis, (at low abundance). The green seaweeds are considered to characterize the biotope and the sensitivty assessments focus on these species with some general information included on Furcellaria lumbricalis and infauna where relevant.
The genus Enteromorpha currently contains 23 taxonomically accepted species (Guiry & Guiry, 2015), although the genus is now more generally accepted as a synonym for Ulva (Hayden et al., 2003). Identification of Ulva to the species level can be problematic and in some instances species can only be distinguished by experts or by genetic analysis and understanding of the taxonomic relationships between green algal species and higher taxonomic levels is rapidly evolving. The sensitivity assessments are largely based on Ulva intestinalis (formerly Enteromorpha intestinalis) and Ulva lactuca, as these are typical characterizing species.
The Ulva sp. that characterize this biotope are classified as opportunistic species that are able to rapidly colonise newly created gaps across a range of sediment types, shore heights, wave exposures and salinity regimes. The life history characteristics that support this opportunism are the broad tolerances for a wide range of conditions (Vermaat & Sand-Jensen, 1987) and high growth and reproduction rates. Ulva sp. release zoospores and gametes (collectively called swarmers) to the water column in high numbers. Ulva sp. can form the swarmers from normal thallus cells that are transformed into reproductive tissue rather than having to produce specialised reproductive structures (Lersten & Voth, 1960), so that a significant portion of the macroalga's biomass is allocated to the formation of zoospores and gametes (Niesenbaum, 1988). Ulva sp. have extended reproduction periods (Smith, 1947) and swarmers are capable of dispersal over a considerable distance. For instance, Amsler & Searles (1980) showed that swarmers of a coastal population of Ulva (as Enteromorpha) reached exposed artificial substrata on a submarine plateau 35 km away.
The supply of swarmers in vast numbers to the coastline (Niesenbaum, 1988) is reflected in the fast recovery rates of this genus. Ulva intestinalis is amongst the first multicellular algae to appear on substrata that have been cleared following a disturbance. For example, following the Torrey Canyon oil spill in March 1967, species of the genus Ulva rapidly recruited to areas where oil had killed the herbivores that usually grazed on them, so that a rapid greening of the rocks (owing to a thick coating of Ulva spp.) was apparent by mid-May (Smith, 1968). The rapid recruitment of Ulva spp. to areas cleared of herbivorous grazers was also demonstrated by Kitching & Thain (1983). Following the removal of the urchin Paracentrotus lividus from areas of Lough Hyne, Ireland, Ulva grew over the cleared area and reached a coverage of 100% within one year (Kitching & Thain, 1983).
Maximum growth of the perennial algae Furcellaria lumbricalis occurs in March/April (Austin, 1960b) and release of carpospores and tetraspores occurs in December/January (Bird et al., 1991). The advantage of being fertile through the winter, as in the case of Furcellaria lumbricalis, is the availability of substrata for colonization as other annual species die back (Kain, 1975). As with all red algae, the spores of Furcellaria lumbricalis are non-flagellate and therefore dispersal is a wholly passive process (Fletcher & Callow, 1992). In general, due to the difficulties of re-entering the benthic boundary layer, it is likely that successful colonization is achieved under conditions of limited dispersal and/or minimum water current activity. It is expected, therefore, that recruitment of Furcellaria lumbricalis would occur from local populations and that establishment and recovery of isolated populations would be patchy and sporadic. Furcellaria lumbricalis is highly fecund, an average sized gametophyte being able to produce approximately 1 million carpospores, or a tetrasporophyte, up to 2 million tetraspores (Austin, 1960a). However, the species grows very slowly compared to other red algae (Bird et al., 1979) and takes a long time to reach maturity. For example, Austin (1960b) reported that in Wales, Furcellaria lumbricalis typically takes 5 years to attain fertility. Christensen (1971) (cited in Bird et al., 1991) noted that following harvesting of Furcellaria lumbricalis forma aegagropila in the Baltic Sea, harvestable biomass had not been regained 5 years after the suspension of harvesting.
The infauna present in this biotope are typically short-lived organisms that grow rapidly and can colonize disturbed environments. Longevity of Tubificoides is two years at which point the worm is sexually mature. It is a hermaphrodite and reproduces throughout the year. The larvae are hatched after about 15 days in a cocoon. The worm can form dense communities, but the dispersal potential is very low (MES Ltd, 2010) suggesting this genus may recover slowly from events that depopulate the biotope. However the species exhibits many of the traits of opportunistic species.
Resilience assessment. The high recovery potential of the Ulva spp. that characterize this biotope, mean that recovery is assessed as ‘High’ (within 2 years) for any level of perturbation (where resistance is ‘None’, ‘Low’, ‘Medium’ or ‘High’. Depending on the season of the impact and level of recovery, the biotope may have recovered within less than six months. Other species may take longer to recolonize, however, the characteristic biotope is considered to have recovered based on the filamentous green seaweeds.
NB: The resilience and the ability to recover from human induced pressures is a combination of the environmental conditions of the site, the frequency (repeated disturbances versus a one off event) and the intensity of the disturbance. Recovery of impacted populations will always be mediated by stochastic events and processes acting over different scales including, but not limited to, local habitat conditions, further impacts and processes such as larval-supply and recruitment between populations. Full recovery is defined as the return to the state of the habitat that existed prior to impact. This does not necessarily mean that every component species has returned to its prior condition, abundance or extent but that the relevant functional components are present and the habitat is structurally and functionally recognisable as the initial habitat of interest. It should be noted that the recovery rates are only indicative of the recovery potential.
The key characterising Ulva spp. are distributed globally and occur in warmer waters than those surrounding the UK suggesting that they can withstand increases in temperature at the pressure benchmark. Ulva spp. are characteristic of upper shore rock pools, where water and air temperatures are greatly elevated on hot days. Empirical evidence for thermal tolerance to anthropogenic increases in temperature is provided by the effects of heated effluents on rocky shore communities in Maine, USA. Ascophyllum and Fucus were eliminated from a rocky shore heated to 27-30 °C by a power station whilst Ulva intestinalis (as Enteromorpha intestinalis) increased significantly near the outfall (Vadas et al., 1976).
The associated red algae Furcellaria lumbricalis has a wide geographic range, occurring in Europe from northern Norway to the Bay of Biscay. Novaczek & Breeman (1990) recorded that specimens of Furcellaria lumbricalis grew well in the laboratory from 0 - 25 °C with optimal growth between 10 and 15 °C. Growth ceased at 25 °C and 100% mortality resulted after 3 months exposure to 27 °C. Similarly, Bird et al. (1979) recorded optimum growth at 15 °C and cessation of growth at 25 °C with associated necrosis of apical segments.
The upper temperature tolerance (that killed half of the test organisms after 96 hours) of the oligochaete Tubificoides benedii (studied as Peloscolex benedeni) was reported to be 28.5 °C (Diaz, 1980).
Sensitivity assessment. Ulva spp., are the key characterising elements that define this biotope and are considered to tolerate increases in temperature at the pressure benchmark. Biotope resistance is therefore assessed as ‘High’ and recovery as ‘High’ (by default) so that the biotope is assessed as ‘Not sensitive’. other associated species, including Furcellaria lumbricalis, are also considered to be 'Not sensitive' to this pressure.
Furcellaria lumbricalis occurrs in Europe from northern Norway to the Bay of Biscay. Novaczek & Breeman (1990) recorded that specimens of Furcellaria lumbricalis grew well in the laboratory from 0-25 °C with optimal growth between 10 and 15 °C. Growth ceased at 25 °C and 100 % mortality resulted after 3 months exposure to 27 °C. Similarly, Bird et al., (1979) recorded optimum growth at 15 °C.
The key species characterising this biotope, Ulva intestinalis and Ulva lactuca, are found in Arctic regions (Guiry & Guiry, 2015 and references therein), Ulva sp. (as Enteromorpha) were reported to be tolerant of a temperature of -20°C (Kylin, 1917). Vermaat & Sand-Jensen (1987) found that rapid deep freezing of Ulva lactuca collected in Roskilde Fjord, Denmark killed the plants. However, individuals from the same area when collected from frozen ice, survived and resumed growth, the plants are able to survive more gradual natural freezing (Vermaat & Sand-Jensen, 1987).
Sensitivity assessment. The presence of Ulva spp. in arctic regions and the freezing tolerances reported by Vermaat & Sand-Jensen (1987) indicate that Ulva spp., would have ‘High’ resistance to decreases in temperature at the acute and chronic benchmarks. The wide temperature tolerance range of Patella vulgata and Littornia saxatilis suggest that the acute and chronic decreases in temperature described by the benchmark would not lead to mortalities. Similarly, based on global temperatures and the link between cooler winter temperatures and reproductive success, Semibalanus balanoides is also considered to be unaffected at the pressure benchmark. Based on the characterising and associated species, this biotope is considered to have ‘High’ resistance and ‘High resilience (by default) to this pressure and is therefore considered to be ‘Not sensitive’. The timing of changes and seasonal weather could result in greater impacts on species. An acute decrease in temperature coinciding with unusually low winter temperatures may exceed thermal tolerances and lead to mortalities of the associated species although this would not alter the character of the biotope.
The biotope typically experiences conditions of full (30-40 psu) or variable salinity (JNCC, 2015). The variable salinity experienced by this biotope maintains the biological assemblage of tolerant species by preventing colonization by species that require higher and more stable salinity (JNCC, 2015). An increase in salinity or a decrease in variability may therefore allow colonization by more competitive species altering the character of the biotope.
The key characterizing Ulva species can survive hypersaline conditions in supralittoral rockpools subjected to evaporation and is considered to be a very euryhaline species, tolerant of extreme salinities ranging from 0 psu to 136 psu (Reed & Russell, 1979). Some variations in salinity tolerance between populations of Ulva intestinalis have been found, however, suggesting that plants have some adaptation to the local salinity regime. Alströem-Rapaport et al., (2010), found that in the brackish Baltic Sea, Ulva intestinalis uses a variety of reproductive modes which was considered to partly explain the high rates of colonisation and adaptability of the species.
Reed & Russell (1979) found that the ability to regenerate from cut thalli varied according to the salinity conditions of the original habitat, and that the pattern of euryhalinity in parental material and offspring was in broad agreement (Reed & Russell, 1979). Eulittoral zone material showed decreased percentage regeneration in concentrated seawater: 51, 68, 95, 102 & 136 psu) when compared to littoral fringe populations of Ulva intestinalis (as Enteromorpha intestinalis). Increased salinity is most likely to occur in the region of the littoral fringe and supralittoral zone and specimens from these areas were able to tolerate very high salinities, a significant decrease in regeneration only being recorded after exposure to concentrated seawater (102 psu and 136 psu) for > 7 days (Reed & Russell, 1979).
Furcellaria lumbricalis is a euryhaline species which occurs in a wide range of salinity conditions down to 6-8 psu (Bird et al., 1991). In the Kattegat and the Gulf of St Lawrence, it is reported to compete well with other species at salinities ranging from 25-32 psu (see review by Bird et al., 1991). Growth experiments in the laboratory revealed that optimum growth occurred at 20 psu, the species grew well at 10 psu and 30 psu, but that growth declined above 30 psu to negligible levels at 50 psu (Bird et al., 1979). It is expected that an increase in salinity may cause reduced growth and fecundity, but that mortality is unlikely.
Sensitivity assessment. Based on reported distributions and the results of experiments to assess salinity tolerance thresholds and behavioural and physiological responses it is considered that Ulva spp. and the associated species would tolerate a change in salinity from variable or reduced to full and some salinity increases above full salinity. As the associated species occur only in low numbers and do not characterise the biotope the sensitivity assessment is based on the Ulva species alone.
The biotope typically experiences conditions of full (30-40 psu) or variable salinity (JNCC, 2015). The key characterizing Ulva species can survive hypersaline conditions in supralittoral rockpools subjected to evaporation and is considered to be a very euryhaline species, tolerant of extreme salinities ranging from 0 psu to 136 psu (Reed & Russell, 1979). Some variation in salinity tolerance between populations of Ulva intestinalis have been found, however, suggesting that plants have some adaptation to the local salinity regime. Alströem-Rapaport et al., (2010), found that in the brackish Baltic Sea, Ulva intestinalis uses a variety of reproductive modes which was considered to partly explain the high rates of colonisation and adaptability of the species. Reed & Russell (1979) found that the ability to regenerate from cut thalli varied according to the salinity conditions of the original habitat, and that the pattern of euryhalinity in parental material and offspring was in broad agreement (Reed & Russell (1979). For example; eulittoral zone material showed decreased percentage regeneration in all salinities (dilute: 0, 4.25, 8.5, 17 & 25.5 psu, and concentrated seawater: 51, 68, 95, 102 & 136 psu) except 34 psu, when compared to littoral fringe populations of Ulva intestinalis (as Enteromorpha intestinalis). None of the eulittoral zone material was able to regenerate in freshwater or concentrated seawater, whilst littoral fringe and rock pool material was able to do so.
Reduced salinity has also been reported to affect the growth rate of Ulva intestinalis. Martins et al. (1999) observed that in years with high precipitation and significant increase of freshwater runoff to the Mondego estuary (west Portugal), that Ulva intestinalis (as Enteromorpha intestinalis) failed to bloom. In the laboratory, the growth rate of Ulva intestinalis was measured against a range of salinities, from 0 to 32 psu. Ulva intestinalis showed the lowest growth rates at extremely low salinity values (less than or equal to 3 psu), and for salinity less than or equal to 1 psu, the algae died. Growth rates at a salinity lower than 5 psu and higher than 25 psu were also low, in comparison to growth between a salinity of 15 and 20 psu, where Ulva intestinalis showed the highest growth rates. Martins et al. (1999) concluded that episodes of reduced salinity were an important external parameter in controlling the growth of Ulva intestinalis. However, elsewhere Ulva intestinalis is known to thrive in areas of the supralittoral zone that receive freshwater runoff. Local conditions may also mediate the ability to tolerate reduced salinities. Kamer & Fong (2001) found that high nitrogen enrichment mitigated the negative effects that reduced salinity had on Ulva intestinalis (as Enteromorpha intestinalis).
Furcellaria lumbricalis occurs in the lowest category on the salinity scale (Connor et al., 2004) and is therefore probably relatively tolerant of decreases in salinity. The species forms extensive populations in the main basin of the Baltic Sea where salinity is 6-8 psu in the upper 60-70 m and its extension into the Gulfs of Bothnia and Finland is limited by the 4 psu isohaline (see review by Bird et al., 1991). However, if the salinity conditions within the habitat were to become freshwater Furcellaria lumbricalis would not be able to survive, as it is a marine species.
Sensitivity assessment. Based on reported distributions and the results of experiments to assess salinity tolerance thresholds and behavioural and physiological responses it is considered that Ulva spp. and the associated species would tolerate a change in salinity from full to variable or reduced to low salinity. As the associated species occur only in low numbers and do not characterise the biotope the sensitivity assessment is based on the Ulva species alone.
This biotope is only found in very weak water flow conditions and a decrease in water flow is considered unlikely to directly affect this biotope, although some reduction in growth may occur where waters experience very little movement so that nutrient supply and recharge of deoxygenated waters is reduced.
The key characterising species of this biotope, Ulva intestinalis and Ulva lactuca are flexible and conform to the direction of water flow reducing drag and breakage. However, experimental studies show that exposure to currents results in sloughing of tissue and higher current velocities result in breakage of the thallus.Kennison & Fong (2013) found that Ulva intestinalis, settled on ceramic tiles and deployed in the field were subject to greater losses at mean flow speeds of 0.2 m/s (approximately 16 % of biomass) than the 8 % loss from individuals subject to lower flows (0.15 m/s). These results agree with those from another study by Flindt et al., (2007) that subjected Ulva sp. and Enteromorpha sp. (description from paper) to increased water flows in flume tanks. Water flow rates were increased from still water incrementally by 0.005 m/s and the amount of biomass sloughed off was measured. At a current speed of 0.12 m/s 3-4% of biomass of Ulva sp. was removed, increasing to 4-7% lost at 0.15 m/s and 40-50% at 0.4 m/s. Enteromorpha sp. were slightly more resistant; at current flows of 0.2 m/s 1% of biomass was sloughed, increasing to 20% at 0.35 m/s. Flindt et al., (2007) estimated from regression models that the current speeds at which all Ulva spp., would be totally removed were 0.82 m/s and 1.28 m/s for Enteromorpha sp. Modelled predictions of thallus breakage based on laboratory studies of Ulva lactuca on bivalve shells estimate that large Ulva lactuca (>50 cm in length) are unlikely to persist where currents exceed 0.5 m/s, whereas smaller individuals (24 cm in length) are unlikely to be present where current speeds exceed 1 m/s (Hawes & Smith, 1995).
Increased water flows may also be beneficial where these enhance recruitment. Increased water velocities can enhance recruitment through increased larval supply (Kennison & Fong, 2013). Houghton et al. (1973) observed that swarmers of Ulva were able to settle onto surfaces subjected to water speeds of up to 10.7 knots, suggesting that changes may not inhibit settlement.
Sensitivity assessment. Increased water flow rates may detach and remove biomass of the Ulva spp, that characterise this biotope. Experiments suggest that the pressure benchmark is biologically relevant, i.e. increases at the pressure benchmark could result in loss and detachment. However as this biotope occurs in sheltered environments and at the benchmark the increase is relatively minor rapid growth of Ulva sp. may mitigate the loss of tissue during the growing season. The experiments do not detail the amount of time that individuals were exposed to flows so that extrapolating the results to predicted losses, particularly for breakage is problematic. Based on the breakage studies (Hawes & Smith, 1995), resistance of Ulva sp., to an increase in water flow at the pressure benchmark is assessed as ‘Medium’ as smaller individuals can persist at flow rates that are almost double those of larger plants and duration of exposure is limited. Resilience is assessed as ‘High’ and sensitivity is assessed as ‘Low’. An increase in water flow at the benchmark is unlikely to have a significant negative effect on the biological composition of the biotope. However, it must be assumed that if there is an increase in the water flow within the biotope there will also be an increase in the water flow around the lagoon (where this biotope occurs in lagoons). This increase could have a detrimental effect on the structure of the lagoon through erosion. This could consequently lead to the loss collapse of a lagoon wall and completely change the physical environment of the biotope, and lead to the loss of the lagoon biotope altogether. A change in the water flow at the pressure benchmark is unlikely to cause the loss of the lagoon biotope.
This biotope occurs in shallow subtidal habitats, shallow examples are not considered to be sensitive to decreased emergence but deeper examples may experience reduced habitat suitability where water depth increases and reduces light penetration. The associated Ulva spp. are able to tolerate desiccation stress and they are often very abundant on the high shore where desiccation stress is the primary factor controlling seaweed distribution, and may even be found above the tidal limits of the shore. Ulva intestinalis (studied as Enteromorpha intestinalis) can survive several weeks of living in completely dried out rock pools, while becoming completely bleached on the uppermost layers, but remaining moist underneath the bleached fronds. However, desiccation stress of germlings may be lower than adults. Hruby & Norton (1979) found that 7-14 day old germlings of Ulva (studied as Enteromorpha) were more tolerant of desiccation than earlier stages, so an increase in desiccation stress may impact more adversely on newly settled germlings than more mature plants. Furcellaria lumbricalis can also be found from the lower intertidal to 12m subtidally (Bunker et al., 2012).
A significant, long-term, increase in emergence placing this biotope fully in the intertidal may lead to replacement of this biotope with one more typical of the changed conditions with Elminuius modestus and littorinids present, a change in grazing pressuire could reduce the biomass of the characterizing, filamentous green algae.
Sensitivity assessment. If shallow sublittoral portions of thebiotope emerged for short periods during the tidal cycle it is considered unlikely that the exposed portions would be negatively impacted, based on the presence of characterizing and associated species in fully intertidal biotopes. Resistance is assessed as 'High' and resilience as 'High' (by default) so that the biotope is considered to be 'Not sensitive'.
This biotope is only found in very and extremely wave sheltered conditions (Connor et al., 2004). Key environmental factors structuring this biotope are variable salinity and the mixed substrata as well as the low level of wave exposure. The characterizing species can be found in biotopes where wave exposure exceeds that experienced by this biotope. A more severe increase in wave action would cause some damage to fronds of filamentous green algae resulting in reduced photosynthesis and compromised growth. Furthermore, individuals may be damaged or dislodged by scouring from sand and gravel mobilized by increased wave action (Hiscock, 1983). Austin (1960b) noted that Furcellaria lumbricalis from extremely exposed sites have smaller dimensions than individuals from semi-exposed sites and that fronds may be lost due to storm action. Sharp et al. (1993) reported Furcellaria lumbricalis found cast ashore following storms.
An increase in wave exposure at the benchmark will not have a significant negative effect on the biological composition of the biotope. However, it might be assumed that if there is an increase in the wave height within the biotope there will also be an increase in the water flow around the lagoon (where this biotope occurs in lagoons). This increase could have a detrimental effect on the structure of the lagoon through erosion. This could consequently lead to the loss collapse of a lagoon wall and completely change the physical environment of the biotope, and lead to the loss of the lagoon biotope altogether.
Sensitivity assessment. An increase in this pressure above the given benchmark has the possibility of removing the lagoon completely. However, at the pressure benchmark, it is very unlikely that the biotope will be affected. Therefore, both the resistance and resilience have been assessed as ‘High’, resulting in a ‘Not sensitive’ assessment.
|Not relevant (NR)||Not relevant (NR)||Not sensitive|
Not sensitive at the pressure benchmark that assumes compliance with all relevant environmental protection standards.
Contamination by non-synthetic chemicals, at levels greater than the pressure benchmark may adversely impact the biotope. The order of metal toxicity to algae varies, with the algal species and experimental conditions, but generally the order is Hg>Cu>Cd>Ag>Pb>Zn (Rice et al., 1973; Rai et al., 1981). The effects of copper on macrophytes have been more extensively studied than the effects of any other metal owing to its use in antifouling paints. Lewis et al. (1998) investigated the influence of copper exposure and heatshock on the physiology and cellular stress response of Ulva intestinalis (as Enteromorpha intestinalis). Heat shock proteins (HSPs) are known to be expressed in response to a variety of stress conditions, including heavy metals (Lewis et al., 1999). Ulva intestinalis was exposed to a range of copper concentrations (0-500 µg -1 for 5 days, to assess the effect of copper exposure on stress proteins (Stress-70 levels) and physiology of the seaweed. Stress-70 was induced by copper exposure, but was found to be no better an indicator of copper exposure than measurement of growth, which is inhibited by copper.
Species of the genus Ulva seem to be especially suitable for monitoring heavy metals in coastal areas and estuaries as it is ubiquitous in both and laboratory experiments have shown that accumulation of Cu, Zn, Cd and Pb by four different species of Ulva (as Enteromorpha) was sufficiently similar to justify pooling samples of the genus for field monitoring (Say et al., 1990). However, the interactions of salinity and temperature with toxicity are not always clear and may hinder cross-comparison of samples and surveys. For instance, Munda (1984) found that the Zn, Mn and Co accumulations in Ulva intestinalis (as Enteromorpha intestinalis) could be enhanced by decreasing the salinity.
|Not relevant (NR)||Not relevant (NR)||Not sensitive|
Not sensitive at the pressure benchmark that assumes compliance with all relevant environmental protection standards.
Hydrocarbon contamination, at levels greater than the benchmark, e.g. from spills of fresh crude oil or petroleum products, may cause significant loss of Ulva spp. Likely effects include smothering, inhibition of respiration and photosynthesis, bleaching and interference with reproduction, so that affected populations may be destroyed. However, the species tends to recover very rapidly from oil pollution incidents. For instance, after the Torrey Canyon tanker oil in 1967, grazing species were killed, and a dense flush of ephemeral green algae (Ulva, Blidingia) appeared on the rocky shore within a few weeks and persisted for up to one year (Smith, 1968).
|Not relevant (NR)||Not relevant (NR)||Not sensitive|
Not sensitive at the pressure benchmark that assumes compliance with all relevant environmental protection standards.
Contamination at levels greater than the benchmark may impact this biotope. Some evidence for adverse effects of chemical pollution on the key characterising species, Ulva intestinalis, has been found. Although herbicides tend not to be used directly in the marine environment, they can enter estuarine areas via river discharge and runoff. Paraquat and 3AT were tested for their effects on the settlement, germination and growth of Ulva (as Enteromorpha) (Moss & Woodhead, 1975). They found that zygotes were able to develop into filaments in the presence of Paraquat at 7 mg/L, but that germination was deferred at higher concentrations. Zygotes demonstrated increased resistance when they settled in clumps on the substratum, and green thalli of Ulva were more susceptible than ungerminated zygotes. Ulva was more intolerant of 3AT than to Paraquat (Moss & Woodhead, 1975).
Synthetic chemicals used as antifouling agents may be directly introduced into the marine environment. Scarlett et al. (1997) analyzed water samples taken from the Plymouth Sound locality for the presence of the s-triazine herbicide, Irgarol 1051, which is an ingredient of antifouling paints used on pleasure boats and ships. Irgarol 1051 was detected at all sampling sites within the Sound; the highest levels were found in close proximity to areas of high boat density, especially where water flow was restricted within marinas, although concentrations within the semi-enclosed Sutton Harbour were less than values predicted from leach rate data. The highest detected concentration of over 120 ng/L significantly inhibited the growth of Ulva intestinalis (as Enteromorpha intestinalis) spores under laboratory conditions; the no effect concentration was 22 ng/L. Photosynthetic efficiency in the adult frond of Ulva intestinalis from Sutton Harbour marina was inhibited by Irgarol 1051 in the laboratory with an EC 50 (72 h) of 2.5 µg/L. A small adverse impact on Ulva intestinalis reproduction within harbours is therefore likely.
Following the Torrey Canyon tanker oil spill, copious amounts of solvent based detergents were sprayed directly on to the shore. Algae on the higher shore was especially affected, and included Ulva intestinalis (as Enteromorpha intestinalis) in high level rock pools where it was killed (Smith, 1968).
The key, characterising Ulva spp. are known to be able to acquire large concentrations of substances from surrounding water. In the vicinity of the Sellafield nuclear plant, England, Ulva (as Enteromorpha) sp. accumulated zirconium, niobium, cerium and plutonium-239, however the species appeared to be unaffected by the radionuclides (Clark, 1997). Based on this evidence, the resistance of the biotope to this pressure at the benchmark, is assessed as 'High', resilience is assessed as 'High' (by default), and the biotope is assessed as 'Not sensitive'.
|Not relevant (NR)||Not relevant (NR)||Not sensitive|
Where nutrients and other factors support rapid growth, large blooms of Cladophora and Ulva spp. can occur, as these die and decay, they can create anoxic conditions in the water column and the sediments they overlay. Some tolerance for anoxia may therefore be expected that allows a proportion of the population to survive and reproduce during and after these conditions.Vermaat & Sand-Jensen (1987) tested the survival of discs of Ulva lactuca during prolonged exposure to anoxia. The 113 mm2 discs were taken from wild plants collected in the Roskilde Fjord, Denmark in late autumn. Anoxic conditions were created in the laboratory by bubbling with N2 gas. Exposure to anoxia for two months did not affect survival but did result in increased respiration and a decrease in growth. Corradi et al., (2006) used similar sized thallus discs from Ulva spp. (113 mm 2), collected from the lagoon Sacca di Goro (Po River Delta) during spring to test the effects of hypoxia on gamete production for Ulva sp. The test oxygen concentrations ranged from 1.78 – 4.02 µmol /L (the benchmark of 2mg/l refers to 64 µmol/L). The exposure to hypoxia was not lethal to the discs and following resumption of normal oxygen conditions gametes were produced.
The effects of reduced oxygenation on the red algae within the biotope are not well studied. Lack of oxygen may impair both respiration and photosynthesis ( Vidaver, 1972). The associated oligochaete Tubificoides benedii inhabits sulfide rich environments and has a high capacity to tolerate anoxic conditions (Nubilier et al., 1997; Giere et al., 1999). Tubificoides benedii is often buried up to 10 cm deep and so has no contact with the surface but has a highly specialized adaptive physiology that allows it to maintain some oxygen consumption even at 2% (approximately 0.18 mg/l) oxygen saturation of the surrounding environment on the Isle of Sylt.
Sensitivity assessment. No direct evidence for the effects of hypoxia on whole plants in-situ was available. However the results of the laboratory experiments which tested parts of Ulva individuals to either prolonged anoxia or short-term hypoxia at levels that exceed the benchmark, indicate that Ulva have ‘High’ resistance to this pressure and ‘High’ resilience by default. Biotope resistance is therefore assessed as ‘High’ and resilience as ‘High’ (no effect to recover from), resulting in a sensitivity of 'Not sensitive'.
This pressure relates to increased levels of nitrogen, phosphorus and silicon in the marine environment compared to background concentrations. The pressure benchmark is set at compliance with Water Framework Directive (WFD) criteria for good status, based on nitrogen concentration (UKTAG, 2014).
The criteria for status under the WFD with regard to nutrient enrichment is concerned with the presence or absence of ‘blooms’ of opportunistic algae , including the key characterising Cladophor and Ulva spp. found in this biotope, that act as indicators of enrichment (eutrophication). The abundance and biomass of these species is used in the implementation of the WFD as indicators to assess condition of waterbodies. The criteria for achieving good status states that there should be: ‘limited cover (<15%) and low biomass (<500g/m2) of opportunistic macroalgal blooms…macroalgae cover shows slight signs of disturbance with slight deviation from reference conditions’ (Wells et al., 2014).
The high abundance and biomass of Ulva spp, that characterise this biotope would suggest that this biotope would fail to achieve ‘good status’. Theoretically, compliance with good status would require a significant loss of characterizing species, suggesting that the biotope would be sensitive to this pressure at the benchmark (i.e. it represents a significant impact for biotope character). However, biotopes dominated by ephemeral green algae may develop in response to chronic physical disturbance from sediment instability or sand-scour, or to reduced salinity and therefore its presence is not necessarily an indicator of abnormal nutrient loading. Typical blooms of opportunistic macroalgae, occur in sheltered areas such as estuaries (Kennison & Fong, 2013) and are likely to form as unattached mats over sediments rather than rocky shores, the character of these is therefore different to the assessed biotope.
Opportunistic algae, including Ulva spp. cannot store nutrients in the thallus (unlike larger, long-lived species) and are adapted to efficiently capture and utilise available nutrients in the water column (Pedersen et al., 2009). A large body of field observations and experiments, surveys and laboratory experiments confirm that the characterising Ulva spp, can utilise high levels of nutrients for growth (Martínez et al., 2012) and that enhanced recruitment (Kraufvelin, 2007) and growth of this genus can occur in enriched areas (Kennison & Fong, 2013, Vaudrey et al., 2010). In areas where nutrient availability is lower either naturally or through management to reduce anthropogenic inputs, Ulva spp. may be negatively affected through reduced growth rate and species replacement (Martínez et al., 2012; Vaudrey et al., 2010).
Sensitivity assessment. If nutrient levels were to increase (exceeding the pressure benchmark) enhanced growth of Ulva spp. would be expected in response and this is not considered to significantly alter the character of the biotope. Ulva spp. may decline in response to reductions in nutrient levels, in habitats where other species more typical of undisturbed species are able to recolonize. However, as this biotope is structured by low salinity, other species are not considered to establish following decreases in nutrient levels and Ulva spp, would be likely to remain the dominant species. The biotope is therefore considered to have ‘High’ resistance to this pressure and ‘High’ resilience, (by default) and is assessed as ‘Not sensitive’.
No empirical evidence was found to support an assessment for the key characterising Ulva spp. Organic enrichment at the pressure benchmark is unlikely to directly affect macroalgae within the biotope. An input of organic matter to the sediment surface will be utilised by the detritus feeders within the sediments.
The oligochaete Tubificoides benedii can be found living in abundance under algal mats (Nubilier et al., 1997). It is opportunistic and responds to organic pollution by increasing the size of the population (Diaz, 1977, cited in Diaz, 1980). Oligochaetes often become the dominant benthic fauna under algal mats (Raffaelli et al., 1998). Estuarine oligochaetes tend to become more abundant in areas where pollution or other physical factors result in a reduced habitat diversity and stressful conditions, concomitant with a decrease in polychaetes species (Diaz, 1980). Barnett (1983) found the maximum abundance of the oligochaete Tubificoides benedii at a site which received a significant input of both industrial and domestic effluent, including raw sewage, in the Humber estuary.
Sensitivity assessment. Overall resistance of the biological assemblage within the biotope is considered to be 'High' and resilience was assessed as 'High', so that this biotope is judged to be 'Not sensitive'.
All marine habitats and benthic species are considered to have a resistance of ‘None’ to this pressure and to be unable to recover from a permanent loss of habitat (resilience is ‘Very Low’). Sensitivity within the direct spatial footprint of this pressure is therefore ‘High’. Although no specific evidence is described confidence in this assessment is ‘High’, due to the incontrovertible nature of this pressure.
This biotope is characterized by the mixed substratum provided by the boulders and cobbles and muddy sediments. Changes to a coarse, clean sediment type or artificial hard substratum would significantly alter the character of the biotope through the loss of the mixed sediments and infauna, although, if the biotope was still sheltered from wave action and exposed to variable salinity, the habitat may still be suitable for typical filamentous algal assemblage. A change to a fine muddy sediment would result in loss of attachment surfaces for green algae, in very wave sheltered areas these may persist as free-growing forms but the typical biotope would be considered to be lost.
Sensitivity assessment. The biotope is considered to have No resistance to this pressure based on a change to a coarse or fine sediment substratum or a hard, free draining substratum. Resilience is assessed as Very low (the pressure is a permanent change) and sensitivity is assessed as High.
|Not relevant (NR)||Not relevant (NR)||Not relevant (NR)|
Not relevant to biotopes occurring on bedrock or on mixed substrata consisting of boulders, cobbles and pebbles.
Removal of the boulders, cobbles and pebbles would remove the attached algae and associated species which are found within the algal turf. Extraction of the muddy sediment would also remove filamentous green algae (where this is growing on sediments) and the associated infauna such as the oligochaetes. Resistance is, therefore, assessed as 'None', recovery of the filamentous green algae is likely to be rapid and resilience is, therefore, assessed as 'High' so that sensitivity is assessed as 'Medium'.
No direct evidence for the sensitivity of filamentous and foliose red algae was found to support assessment of this pressure. The species characterizing this biotope occur on the rock and therefore have no protection from abrasion at the surface. In a recent review, assigning species to groups based on tolerances to bottom disturbance from fisheries, the sponge Halichondria panicea were assigned to AMBI Fisheries Group II, described as ‘species sensitive to fisheries in which the bottom is disturbed, but their populations recover relatively quickly' (Gittenberger & van Loon, 2011).
Sensitivity assessment. The impact of surface abrasion will depend on the footprint, duration and magnitude of the pressure. In response to a single event of abrasion a proportion of the populations of the characterizing and associated species may be removed, but damaged algal individuals, in-situ would be capable of growth and reproduction. Resistance of the biotope, to a single abrasion event is assessed as ‘Low’ and recovery as ‘High’, so that sensitivity is assessed as ‘Low’.
The cobbles and pebbles in the biotope are likely to move as a result of penetration and/or sub surface disturbance. The characterising and associated species would probably accrue damage from abrasion and scour and attached algae trapped on the undersides of overturned pebbles would be unable to photosynthesise and are likely to be smothered. Penetration and disturbance is also likely to harm infauna.
Sensitivity assessment. This biotope is considered to have 'Low' resistance and 'High' resilience, to this pressure and sensitivity is therefore assessed as 'Low'.
Siltation, which may be associated with increased suspended solids is assessed separately. As a photoautotroph, the key characterising Ulva spp., is likely to benefit from reduced turbidity, as the light attenuating effects of turbid water reduce photosynthesis. However experiments have shown that Ulva is a shade tolerant species and can compensate for reduced irradiance by increasing chlorophyll concentration and light absorption at low light levels. Ulva spp. were able to survive over two months in darkness and to begin photosynthesising immediately when returned to the light (Vermaat & Sand-Jensen, 1987). Limited shading from suspended sediments is therefore not considered to negatively affect this genus. Suspended sediments may however have abrading effects on the fronds of Ulva spp. Tolhurst et al. (2007) found that Ulva intestinalis germlings kept in tanks and exposed to 100 mg/l of suspended sediment showed reduced growth. Similarly, Hyslop & Davies (1998) found that Ulva lactuca lost weight when kept in flasks with 1 g/l of colliery waste that was shaken for 1 hour every day for 8 days. The experimental solids level, however, exceeds the pressure benchmark.
Furcellaria lumbricalis is tolerant of sand cover and scour. Therefore, the algal species which characterize the biotope are not likely to be affected directly by an increase increase in scour which could be caused by a change in suspended sediment. However, increased suspended sediment will decrease light availability. Furcellaria lumbricalis often occurs in relatively turbid waters. Laboratory experiments by Bird et al. (1979) revealed that Furcellaria lumbricalis was growth saturated at very low light levels (ca 20µE/m²/s) compared to other algae such as Chondrus crispus (50-60µE/m²/s). They suggest that this may be an explanation why Furcellaria lumbricalis is able to proliferate in relatively deep and turbid waters. Similarly, in their review, Bird et al. (1979) comment that in all studies, saturation and inhibition radiances were low for Furcellaria lumbricalis compared to other macroalgae indicating good competitive ability in the attenuated light of deeper or more turbid waters. Increases in turbidity may provide the species with a competitive advantage over other macroalgae.
Sensitivity assessment. The biotope is considered to be ‘Not sensitive’ to a reduction in suspended solids. The negligible water flows and the very sheltered to extremely wave sheltered conditions within this biotope mean that an increase in suspended sediment would not cause an increase in the level of scour within this biotope. A change in light attenuation may result in a decrease in growth and biomass of algae although both Ulva spp and Furcellaria lumbricalis are likely to survive. Both resistance and resilience have been assessed as ‘High’, resulting in a ‘Not sensitive’ assessment.
Observations and experiments indicate that Ulva spp. have relatively high tolerances for the stresses induced by burial (darkness, hypoxia and exposure to sulphides). Vermaat & Sand-Jensen (1987) exposed thallus discs (113 mm2) of Ulva lactuca to darkness and anoxia and sulphides at winter temperatures. It was found that these conditions did not affect survival over two months, although exposure to anoxia increased respiration and reduced growth (Vermaat & Sand-Jensen, 1987). These experiments were undertaken using Ulva lactuca collected from Roskilde Fjord, Denmark. Corradi et al., (2006) subjected Ulva sp. collected from the Sacca di Goro, Italy to similar stressors (hypoxia 1.78 – 4.02 µmol /L, or sulphide at 1mM, both treatments in darkness) for 3,5 or 7days at 20oC. The thallus discs survived but no gametes were produced until recovery in oxygenated conditions. The high tolerance of darkness, anoxia and hydrogen sulphides allows buried fragments of Ulva sp. to overwinter, protected from frosts. Kamermans et al., (1998) found that parts of Ulva thalli that were collected from the Veerse Meer lagoon in the Netherlands could resume growth in the spring when returned to the surface. Ulva spp. in sheltered areas are often unattached to the substratum and therefore are not considered a direct proxy for attached Ulva spp. in this biotope.
Ulva lactuca is a dominant species on sand-affected rocky shores in New Hampshire (Daly & Mathieson, 1977) although Littler et al., (1983) suggest that Ulva sp., are present in areas periodically subject to sand deposition not because they are able to withstand burial but because they are able to rapidly colonise sand-scoured areas (such as this biotope). Ulva spp. have, however, been reported to form turfs that trap sediments (Airoldi, 2003, references therein) suggesting that resistance to chronic rather than acute siltation events may be higher. In general, propagules, early post-settlement stages and juveniles suffer severe stress and mortality from sediments (Airoldi, 2003). Hyslop et al. (1997) compared the composition, abundance and distribution of dominant plants and animals at several rocky shores affected or unaffected by dumping of colliery wastes along the coastline of northeast England. They reported that while the distribution of animals was not related to colliery wastes, diversity of macroalgae was significantly negatively correlated with colliery waste inputs and particularly dramatic reductions in cover at the affected sites were observed for Ulva lactuca. The authors suggested that, because colliery waste leaches much of its toxic chemical content into the sea, detrimental effects were most likely related to the physical presence of sediments.
Sensitivity assessment. A covering of sediment to a depth of 5 cm is likely to partially cover erect Cladophora spp. and may fully cover the flexible Ulva spp. Unless the sediment is removed by currents or wave action photosynthesis would be inhibited and fronds of macroalgae may begin to decay. As this biotope occurs in sheltered habitats sediments may be shifted rather than removed, so that exposure to this pressure is prolonged. The available evidence indicates that Ulva spp. can survive some of the stressors associated with burial but would be sensitive to abrasion and scouring forces resulting from the deposition and removal of sediments. The sensitivity assessment for the biotope is based on Ulva spp. Siltation by 5 cm of fine sediments is considered to remove a proportion of the population through smothering and scour effects and resistance is assessed as ‘Low’, recovery is assessed as ‘High’ and sensitivity is assessed as ‘Low’.
Observations and experiments indicate that Ulva spp. have relatively high tolerances for the stresses induced by burial (darkness, hypoxia and exposure to sulphides). Vermaat & Sand-Jensen , (1987) exposed thallus discs (113 mm2) of Ulva lactuca to darkness and anoxia and sulphides at winter temperatures. It was found that these conditions did not affect survival over two months, although exposure to anoxia increased respiration and reduced growth (Vermaat & Sand-Jensen, 1987). These experiments were undertaken using Ulva lactuca collected from Roskilde Fjord, Denmark. Corradi et al., (2006) subjected Ulva sp. collected from the Sacca di Goro, Italy to similar stressors (hypoxia 1.78 – 4.02 µmol /L, or sulphide at 1mM, both treatments in darkness) for 3, 5 or 7days at 20oC. The thallus discs survived but no gametes were produced until recovery in oxygenated conditions. The high tolerance of darkness, anoxia and hydrogen sulphides allows buried fragments of Ulva sp. to overwinter, protected from frosts. Kamermans et al., (1998) found that parts of Ulva thalli that were collected from the Veerse Meer lagoon in the Netherlands could resume growth in the spring when returned to the surface. Ulva spp. in sheltered areas are often unattached to the substratum and therefore are not considered a direct proxy for attached Ulva spp. in this biotope.
Although Ulva spp. present in sedimentary habitats may be able to survive the chemical stress of burial and re-grow from surviving fragments, evidence for attached individuals from rocky shores suggest that resistance to this pressure may be lower. Ulva lactuca is a dominant species on sand-affected rocky shores in New Hampshire (Daly & Mathieson, 1977), although Littler et al., (1983) suggest that Ulva sp., are present in areas periodically subject to sand deposition not because they are able to withstand burial but because they are able to rapidly colonise sand-scoured areas (such as this biotope). Ulva spp. have, however, been reported to form turfs that trap sediments (Airoldi, 2003, references therein) suggesting that resistance to low-level chronic rather than acute siltation events may be higher. In general, propagules, early post-settlement stages and juveniles suffer severe stress and mortality from sediments (Airoldi, 2003). Hyslop et al. (1997) compared the composition, abundance and distribution of dominant plants and animals at several rocky shores affected or unaffected by dumping of colliery wastes along the coastline of northeast England. They reported that while the distribution of animals was not related to colliery wastes, diversity of macroalgae was significantly negatively correlated with colliery waste inputs and particularly dramatic reductions in cover at the affected sites were observed for Ulva lactuca. The authors suggested that, because colliery waste leaches much of its toxic chemical content into the sea, detrimental effects were most likely related to the physical presence of sediments.
Sensitivity assessment. The available evidence indicates that Ulva spp. can survive some of the stressors associated with burial but would be sensitive to abrasion and scouring forces resulting from the deposition and removal of sediments. As this biotope occurs in habitats sheltered from currents and wave action the deposit of fine sediment is likely to remain in-situ for prolonged periods nad may be moved rather than removed and shallow examples of this habitat mey even be infilled. Siltation by 30 cm of fine sediment is therefore considered to remove most of the filamentous green algae and red algae and likely to smother infauna, resistance is assessed as ‘None’, recovery is assessed as ‘High’ (following habitat recovery) and sensitivity is assessed as ‘Medium’.
|Not Assessed (NA)||Not Assessed (NA)||Not assessed (NA)|
|No evidence (NEv)||No Evidence (NEv)||No evidence (NEv)|
|Not relevant (NR)||Not relevant (NR)||Not relevant (NR)|
A number of experiments have demonstrated that the key characterising species Ulva lactuca, has high tolerance for shading and can survive periods of darkness. Vermaat & Sand-Jensen (1987) found that Ulva lactuca, collected from Roskilde Fjord in Denmark in late autumn had extremely high shade tolerances. Increasing chlorophyll concentration and light absorption allowed the individuals (studied experimentally as thallus discs of 113mm2) to continue to grow at the lowest irradiance tested (0.6 µE m2/s). This corresponds to the lowest light-levels experienced by deep-living marine macroalgae and phytoplankton growing under ice (Vermaat & Sand-Jensen, 1987). Ulva lactuca was able to survive two months in darkness and was able to resume growth immediately when transferred to the light (Vermaat & Sand-Jensen, 1987).
The red algae Furcellaria lumbricalis often occurs in relatively turbid waters. Laboratory experiments by Bird et al. (1979) revealed that Furcellaria lumbricalis was growth saturated at very low light levels (ca 20 µE/m²/s) compared to other algae such as Chondrus crispus (50 - 60 µE/m²/s) and Fucus serratus (100 µE/m²/s). They suggest that this may be an explanation why Furcellaria lumbricalis is able to proliferate in relatively deep and turbid waters. Similarly, in their review, Bird et al. (1979) comment that in all studies, saturation and inhibition radiances were low for Furcellaria lumbricalis compared to other macroalgae indicating good competitive ability in the attenuated light of deeper or more turbid waters.
Sensitivity assessment. The key Ulva spp. that characterises the biotope are considered to have ‘High’ resistance to changes in light level, although extreme changes such as complete darkness would prevent photosynthesis and growth and high light levels may be damaging. Recovery is assessed as ‘High’ by default and the biotope is judged to be ‘Not sensitive ‘.
No direct evidence was found to assess this pressure. This biotope occurs in sheltered areas and recruitment from within the biotope may be more important in sustaining the population than water transport of propagules from outside the habitat.
The key characterizing Ulva spp. produce large amounts of motile swarmers, throughout the growing season (Niesenbaum, 1988) . The level of supply of potential recruits is considered to be so great that barriers and changes in tidal excursion will not negatively impact populations. The associated species Furcellaria lumbricalis produce spores that are transported by water movements. Barriers that reduce the degree of tidal excursion may alter larval supply to suitable habitats from source populations. Conversely the presence of barriers may enhance local population supply by preventing the loss of larvae from enclosed habitats. As the key characterizing Ulva spp. species are widely distributed and have larvae capable of long distance transport, resistance to this pressure is assessed as 'High' and resilience as 'High' by default. This biotope is therefore considered to be 'Not sensitive'.
|Not relevant (NR)||Not relevant (NR)||Not relevant (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)|
The key characterizing Cladophora and Ulva spp. may be cultivated for use as biofilters to mitigate pollution, as biomass for biofuel generation or for pharmaceuticals and food. No information was found on current production in the UK and no evidence was found for the effects of gene flow between cultivated species and wild populations. As wild populations are widely distributed and water flow may aid dispersal of swarmers, populations are not considered to be genetically isolated. It is therefore considered that resistance to changes in genetic structure are ‘High’ and that resilience is therefore ‘High’ by default and the biotope is ‘Not sensitive’. The use of genetically modified organisms in the future, which may transfer novel genetic material to wild populations may result in harmful impacts and this assessment would require updating if such scenarios arise.
The non-native hydroid, Cordylophora caspia, may compete directly with native species for food and space and is found in estuaries and brackish water (from 2-17psu), this biotope may therefore provide suitable habitat (Sweet, 2011i).
In Canada green sea fingers Codium fragile fragile, formerly Codium fragile subsp tormentosoides) has displaced native seaweed species and become the dominant canopy species in some areas, consequently altering community structure and composition, where conditions permit. Most significant impacts have occurred where algal diversity in the invaded area is low. In the UK algal diversity is high and green sea fingers has not yet occurred in nuisance densities (Sweet, 2011j). Generally this species occurs on more sheltered shores and in estuaries and the habitats in which this biotope occurs, where algal diversity is low, may potentially be colonized.
Sensitivity assessment. The low salinity habitat that this biotope is found in may not provide suitable habitat for many INIS. Based on the current lack of information on invasion by INIS resistance is assessed as 'High and resilience as 'High' by default so that the biotope is assessed as 'Not sensitive'. This assessment may require updating in the future as more information becomes available or as distribution patterns of INIS change.
No evidence was found that outbreaks of microbial pathogens significantly impact populations of the key characterizing Ulva spp. Macroalgae produce protective chemical defences against pathogens with production of antimicrobial and antifungal agents. Barton (1901) noted that Furcellaria lumbricalis may become infested with nematode worms and reacts by gall formation.
Sensitivity assessment. Based on the lack of evidence for mass mortalities of the characterizing green algal species within this biotope, resistance to this pressure is assessed as ‘High’ and recovery as ‘High’ (by default) so that the biotope is considered to be ‘Not sensitive’.
Direct, physical impacts from harvesting are assessed through the abrasion and penetration of the seabed pressures. The sensitivity assessment for this pressure considers any biological/ecological effects resulting from the removal of target species on this biotope. The key characterizing Ulva spp. may be collected from the wild for use in pharmaceuticals and food. Removal of this species in high quantities would alter the character of the biotope, resulting in reclassification. Resistance to harvesting is assessed as ‘Low’ as the genus, is relatively large, attached and accessible and therefore has no escape or other avoidance mechanisms. Resilience is assessed as ‘High’ as cleared areas will be readily colonised. Sensitivity is therefore assessed as ‘Low’.
Extraction of Furcellaria lumbricalis was reviewed by Guiry & Blunden (1991). Plinski & Florczyk (1984) noted that over-exploitation of Furcellaria lumbricalis resulted in severe depletion of stocks. However, no commercial harvest as yet occurs in Britain or Ireland. Due to the relative small size of the population within this biotope, even small scale hand collecting may have a significant effect, should this species be targeted in the future. The infauna present in the biotope are not targeted.
Sensitivity assessment. Resistance is assessed as 'Low' as the targeted species are attached, conspicuous and accessible (where this biotope occurs at the sublittoral fringe). Resilience is assessed as 'High', based on the characterizing green seaweeds and sensitivity is therefore assessed as 'Low'.
Incidental removal of the characterizing filamentous green seaweeds would alter the character of the biotope. The ecological services such as primary production provided by these species would also be lost.
Sensitivity assessment. Removal of a large percentage of the characterizing species would alter the character of the biotope, so that it was bare rock. Resistance is therefore assessed as ‘Low’ and recovery as ‘High’ and sensitivity is therefore assessed as 'Low'.
|UK Biodiversity Action Plan Priority|
The biotope is likely to show a high degree of change both seasonally and from year to year. Populations of algae, fish, mysids, ascidians and other species are likely to fluctuate whilst patches of deoxygenated/Beggiatoa covered sediment and seaweed are to be expected in varying amounts.
Aaser, H.F., Jeppesen, E. & Soendergaard, M., 1995. Seasonal dynamics of the mysid Neomysis integer and its predation on the copepod Eurytemora affinis in a shallow hypertrophic brackish lake. Marine Ecology Progress Series, 127, 47-56.
Airoldi, L., 2003. The effects of sedimentation on rocky coast assemblages. Oceanography and Marine Biology: An Annual Review, 41,161-236
Alströem-Rapaport, C., Leskinen, E. & Pamilo, P., 2010. Seasonal variation in the mode of reproduction of Ulva intestinalis in a brackish water environment. Aquatic Botany, 93 (4), 244-249.
Amsler, C.D. & Searles, R.B., 1980. Vertical distribution of seaweed spores in a water column off shore of North Carolina. Journal of Phycology, 16, 617-619.
Austin, A.P., 1960a. Life history and reproduction of Furcellaria fastigiata (L.) Lamouroux. Annals of Botany, New Series, 24, 257-274.
Austin, A.P., 1960b. Observations on the growth, fruiting and longevity of Furcellaria fastigiata (L.) Lamouroux. Hydrobiologia, 15, 193-207.
Barnett, B.E., 1983. Oligochaetes as indicators of pollution in the Humber estuary, with special reference to Tubificoides benedii. Environmental Pollution (Series A), 30, 277-291.
Barton, E.S., 1901. On certain galls in Furcellaria and Chondrus. Journal of Botany, 39, 49-51.
Bird, C.J., Saunders, G.W. & McLachlan, J., 1991. Biology of Furcellaria lumbricalis (Hudson) Lamouroux (Rhodophyta: Gigartinales), a commercial carrageenophyte. Journal of Applied Phycology, 3, 61-82.
Bird, N.L., Chen, L.C.-M. & McLachlan, J., 1979. Effects of temperature, light and salinity of growth in culture of Chondrus crispus, Furcellaria lumbricalis, Gracilaria tikvahiae (Gigartinales, Rhodophyta), and Fucus serratus (Fucales, Phaeophyta). Botanica Marina, 22, 521-527.
Bunker, F., Maggs, C., Brodie, J. & Bunker, A., 2012. Seasearch Guide to Seaweeds of Britain and Ireland. Marine Conservation Society, Ross-on-Wye.
Burrows, E.M., 1991. Seaweeds of the British Isles. Volume 2. Chlorophyta. London: British Museum (Natural History).
Christensen, J., 1971. Furcellaria fastigiata (Huds.) Lamour. - an important commercial seaweed. In Proceedings, Meeting on the Canadian Atlantic Seaweeds Industry, Oct, 5-6, 1971, Charlottetown. Industrial Development Branch, Fisheries Service, Environment Canada, Ottawa, pp. 23–27.
Clark, R.B., 1997. Marine Pollution, 4th ed. Oxford: Carendon Press.
Connor, D.W., Allen, J.H., Golding, N., Howell, K.L., Lieberknecht, L.M., Northen, K.O. & Reker, J.B., 2004. The Marine Habitat Classification for Britain and Ireland. Version 04.05. Joint Nature Conservation Committee, Peterborough. www.jncc.gov.uk/MarineHabitatClassification.
Corradi, M.G., Gorbi, G. & Zanni, C., 2006. Hypoxia and sulphide influence gamete production in Ulva sp. Aquatic Botany, 84 (2), 144-150.
Daly, M.A. & Mathieson, A.C., 1977. The effects of sand movement on intertidal seaweeds and selected invertebrates at Bound Rock, New Hampshire, USA. Marine Biology, 43, 45-55.
Diaz, R.J., 1980. Ecology of tidal freshwater and estuarine Tubificidae (Oligochaeta). In Aquatic oligochaete biology, Proceedings of the first international symposium on aquatic oligochaete biology, Sydney, British Colombia, Canada, May 1-4, 1979, (ed. R.O. Brinkhurst & D.G. Cook), pp. 319-330. New York: Plenum Press.
Fletcher, R.L. & Callow, M.E., 1992. The settlement, attachment and establishment of marine algal spores. British Phycological Journal, 27, 303-329.
Flindt, M.R., Pedersen, C.B., Amos, C.L., Levy, A., Bergamasco, A. & Friend, P., 2007. Transport, sloughing and settling rates of estuarine macrophytes: Mechanisms and ecological implications. Continental Shelf Research, 27 (8), 1096-1103.
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.
Guiry, M.D. & Blunden, G., 1991. Seaweed Resources in Europe: Uses and Potential. Chicester: John Wiley & Sons.
Guiry, M.D. & Guiry, G.M. 2015. AlgaeBase [Online], National University of Ireland, Galway [cited 30/6/2015]. Available from: http://www.algaebase.org/
Hawes, I. & Smith, R., 1995. Effect of current velocity on the detachment of thalli of Ulva lactuca (Chlorophyta) in a New Zealand estuary. Journal of Phycology, 31 (6), 875-880.
Hayden, H.S., Blomster, J., Maggs, C.A., Silva, P.C., Stanhope, M.J. & Waaland, J.R., 2003. Linnaeus was right all along: Ulva and Enteromorpha are not distinct genera. European Journal of Phycology, 38, 277-294.
Hiscock, K., 1983. Water movement. In Sublittoral ecology. The ecology of shallow sublittoral benthos (ed. R. Earll & D.G. Erwin), pp. 58-96. Oxford: Clarendon Press.
Hough, A.R. & Naylor, E., 1992. Distribution and position maintenance behaviour of the estuarine mysid Neomysis integer. Journal of the Marine Biological Association of the United Kingdom, 72, 869-876.
Houghton, D.R., Pearman, I. & Tierney, D., 1973. The effect of water velocity on the settlement of swarmers of the green alga Enteromorpha. In Proceedings of the third international congress on marine corrosion and fouling (ed. R.F. Acker, B. Floyd Brown, J.R. DePalma & W.P. Iverson), 682-690. Evanston, Northwestern University Press.
Hruby, T. & Norton, T.A., 1979. Algal colonization on rocky shores in the Firth of Clyde. Journal of Ecology, 67, 65-77.
Hyslop, B.T. & Davies, M.S., 1998. Evidence for abrasion and enhanced growth of Ulva lactuca L. in the presence of colliery waste particles. Environmental Pollution, 101 (1), 117-121.
Hyslop, B.T., Davies, M.S., Arthur, W., Gazey, N.J. & Holroyd, S., 1997. Effects of colliery waste on littoral communities in north-east England. Environmental Pollution, 96 (3), 383-400.
JNCC, 2015. The Marine Habitat Classification for Britain and Ireland Version 15.03. JNCC: JNCC. 2015(20/05/2015). jncc.defra.gov.uk/MarineHabitatClassification
Kain, J.M., 1975a. Algal recolonization of some cleared subtidal areas. Journal of Ecology, 63, 739-765.
Kamer, K. & Fong, P., 2001. Nitrogen enrichment ameliorates the negative effects of reduced salinity on green macroalga Enteromorpha intestinalis. Marine Ecology Progress Series, 218, 87-93.
Kamermans, P., Malta, E.-j., Verschuure, J.M., Lentz, L.F. & Schrijvers, L., 1998. Role of cold resistance and burial for winter survival and spring initiation of an Ulva spp.(Chlorophyta) bloom in a eutrophic lagoon (Veerse Meer lagoon, The Netherlands). Marine Biology, 131 (1), 45-51.
Kennison, R.L. & Fong, P., 2013. High amplitude tides that result in floating mats decouple algal distribution from patterns of recruitment and nutrient sources. Marine Ecology Progress Series, 494, 73-86.
Kitching, J.A. & Thain, V.M., 1983. The ecological impact of the sea urchin Paracentrotus lividus (Lamarck) in Lough Ine, Ireland. Philosophical Transactions of the Royal Society of London, Series B, 300, 513-552.
Kraufvelin, P., 2007. Responses to nutrient enrichment, wave action and disturbance in rocky shore communities. Aquatic Botany, 87 (4), 262-274.
Krause-Jensen, D., McGlathery, K., Rysgaard, S. & Christensen, P.B., 1996. Production within dense mats of filamentous macroalga Chaetomorpha linum in relation to light and nutrient availability. Marine Ecology Progress Series, 134, 207-216.
Kylin, H., 1917. Kalteresistenze der Meerealen. Bericht der Deutschen Botanischen Gesellschafter, 35, 370-384.
Lersten, N.R. & Voth, P.D., 1960. Experimental control of zoid discharge and rhizoid formation in the green alga Enteromorpha. Botanical Gazette, 122, 33-45.
Lewis, S., Handy, R.D., Cordi, B., Billinghurst, Z. & Depledge, M.H., 1999. Stress proteins (HSPs): methods of detection and their use as an environmental biomonitor. Ecotoxicology, 8, 351-368.
Lewis, S., May, S., Donkin, M.E. & Depledge, M.H., 1998. The influence of copper and heat shock on the physiology and cellular stress response of Enteromorpha intestinalis. Marine Environmental Research, 46, 421-424.
Martínez, B., Arenas, F., Rubal, M., Burgués, S., Esteban, R., García-Plazaola, I., Figueroa, F., Pereira, R., Saldaña, L. & Sousa-Pinto, I., 2012. Physical factors driving intertidal macroalgae distribution: physiological stress of a dominant fucoid at its southern limit. Oecologia, 170 (2), 341-353.
Martins, I., Oliveira, J.M., Flindt, M.R. & Marques, J.C., 1999. The effect of salinity on the growth rate of the macroalgae Enteromorpha intestinalis (Chlorophyta) in the Mondego estuary (west Portugal). Acta Oecologica, 20 (4), 259-265.
MES, 2010. Marine Macrofauna Genus Trait Handbook. Marine Ecological Surveys Limited. http://www.genustraithandbook.org.uk/
Moore, P.G., 1977a. Inorganic particulate suspensions in the sea and their effects on marine animals. Oceanography and Marine Biology: An Annual Review, 15, 225-363.
Moss, B.L. & Woodhead, P., 1975. The effect of two commercial herbicides on the settlement, germination and growth of Enteromorpha. Marine Pollution Bulletin, 6, 189-192.
Munda, I.M., 1984. Salinity dependent accumulation of Zn, Co and Mn in Scytosiphon lomentaria (Lyngb.) Link and Enteromorpha intestinalis (L.) from the Adriatic Sea. Botanica Marina, 27, 371-376.
Niesenbaum R.A., 1988. The ecology of sporulation by the macroalga Ulva lactuca L. (chlorophyceae). Aquatic Botany, 32, 155-166.
Novaczek, I. & Breeman, A.M., 1990. Thermal ecotypes of amphi-Atlantic algae. 2. Cold-temperate species (Furcellaria lumbricalis and Polyides rotundus). Helgolander Meeresuntersuchungen, 44, 475-485.
Nubilier, N., Windoffer, R., Grieshaber, M.K. & Giere, O., 1997. Ultrastructure and anaerobic metabolism of mitochondria in the marine oligochaete Tubificoides benedii: effects of hypoxia and sulfide. Marine Biology, 127, 637-645.
Pedersen, M.F. & Borum, J., 1996. Nutrient control of algal growth in estuarine waters. Nutrient limitation and the importance of nitrogen requirements and nitrogen storage among phytoplankton and species of macroalgae. Marine Ecology Progress Series, 142, 262-272.
Pedersen, M.F., Borum, J. & Fotel, L. F., 2009. Phosphorus dynamics and limitation of fast and slow-growing temperate seaweeds in Oslofjord, Norway. Marine Ecology Progress Series, 399, 103-115
Plinski, M. & Florczyk, I., 1984. Changes in the phytobenthos resulting from the eutrophication of Puck Bay. Limnologica, 15, 325-327.
Raffaelli, D.G., Raven, J.A. & Poole, L.J., 1998. Ecological impact of green macroalgal blooms. Oceanography and Marine Biology: an Annual Review, 36, 97-125.
Rai, L., Gaur, J.P. & Kumar, H.D., 1981. Phycology and heavy-metal pollution. Biological Reviews, 56, 99-151.
Reed, R.H. & Russell, G., 1979. Adaptation to salinity stress in populations of Enteromorpha intestinalis (L.) Link. Estuarine and Coastal Marine Science, 8, 251-258.
Rice, H., Leighty, D.A. & McLeod, G.C., 1973. The effects of some trace metals on marine phytoplankton. CRC Critical Review in Microbiology, 3, 27-49.
Riisgård, H.U., Bondo Christensen, P., Olesen, N.J., Petersen, J.K, Moller, M.M. & Anderson, P., 1993. Biological structure in a shallow cove (Kertinge Nor, Denmark) - control by benthic nutrient fluxes and suspension-feeding ascidians and jellyfish. Ophelia, 41, 329-344.
Say, P.J., Burrows, I.G. & Whitton, B.A., 1990. Enteromorpha as a monitor of heavy metals in estuaries. Hydrobiologia, 195, 119-126.
Scarlett, A., Donkin, M.E., Fileman, T.W. & Donkin, P., 1997. Occurrence of the marine antifouling agent Irgarol 1051 within the Plymouth Sound locality: implications for the green macroalga Enteromorpha intestinalis. Marine Pollution Bulletin, 38, 645-651.
Sharp, G.J., Tetu, C., Semple, R. & Jones, D., 1993. Recent changes in the seaweed community of western Prince Edward Island: implications for the seaweed industry. Hydrobiologia, 260-261, 291-296.
Smith, G.M., 1947. On the reproduction of some Pacific coast species of Ulva. American Journal of Botany, 34, 80-87.
Smith, J.E. (ed.), 1968. 'Torrey Canyon'. Pollution and marine life. Cambridge: Cambridge University Press.
Sweet, N.S. 2011j. Green sea-fingers (tomentosoides), Codium fragile subsp. tomentosoides. Great Britain Non-native Species Secretariat. [cited 16/06/2015]. Available from: <http://www.nonnativespecies.org
Sweet N.S., 2011i. Freshwater hydroid, Cordylophora caspia. GB Non-native species secretariat, [On-line]. [cited 24/02/16]. Available from:
Taylor, A.R.A., 1970. Studies of the Biology and Ecology of Chondrus crispus Stack on Prince Edward Island. Progress Report No. 35, 30 pp.
Thompson, T.E. & Seaward, D.R. 1989. Ecology and taxonomic status of the aplysiomorph Akera bullata in the British Isles. Journal of Molluscan Studies, 55, 489-496.
Tolhurst, L.E., Barry, J., Dyer, R.A. & Thomas, K.V., 2007. The effect of resuspending sediment contaminated with antifouling paint particles containing Irgarol 1051 on the marine macrophyte Ulva intestinalis. Chemosphere, 68 (8), 1519-1524.
UKTAG, 2014. UK Technical Advisory Group on the Water Framework Directive [online]. Available from: http://www.wfduk.org
Vadas, R.L., Keser, M. & Rusanowski, P.C., 1976. Influence of thermal loading on the ecology of intertidal algae. In Thermal Ecology II, (eds. G.W. Esch & R.W. McFarlane), ERDA Symposium Series (Conf-750425, NTIS), Augusta, GA, pp. 202-212.
Vaudrey, J.M.P., Kremer, J.N., Branco, B.F. & Short, F.T., 2010. Eelgrass recovery after nutrient enrichment reversal. Aquatic Botany, 93 (4), 237-243.
Vermaat J.E. & Sand-Jensen, K., 1987. Survival, metabolism and growth of Ulva lactuca under winter conditions: a laboratory study of bottlenecks in the life cycle. Marine Biology, 95 (1), 55-61.
Vidaver, W., 1972. Dissolved gases - plants. In Marine Ecology. Volume 1. Environmental factors (3), (ed. O. Kinne), 1471-1490. Wiley-Interscience, London.
Wells, E., Best, M., Scanlan, C. & Foden, J., 2014. Opportunistic Macroalgae Blooming. Water Framework Directive- development of classification tools for ecological assessment., Water Framework Directive-United Kingdom Technical Advisory Group (WFD-UKTAG),
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Last Updated: 23/03/2016