The Marine Life Information Network

The southern-most distribution of Urospora penicilliformis in the northern Hemisphere is limited by the 26°S and 16°W isotherm (Bischoff & Wiencke, 1995). Samples of Urospora penicilliformis were grown in the laboratory for two weeks at a range of temperatures. Cold temperate samples in the Northern Hemisphere grew between 0-20°C and survived up to 25-26°C. Arctic strains survive up to 23-24°C while Antarctic strains survive up to 19°C (Bischoff & Wiencke, 1995).

This biotope is characteristic of the littoral fringe, where it is rarely inundated, but exposed to direct sunlight for prolonged periods, warm weather in summer and frost and ice in winter. Urospora sp. are most abundant in winter to spring and sometimes summer, while Ulothrix is most abundant in summer so that increases in temperature may change to the relative abundance of the species within the biotope.  However, the temperature will also affect water retention and desiccation, so that the effect of temperature change will also vary depending on the wave exposure, splash, and spray, humidity and cloud cover.  Nevertheless, the wide distribution of both species in the North Hemisphere suggests that the biotope is resistant of temperature change at the benchmark level.  Therefore, resistance is probably High, resilience is High (by default) and the biotope is assessed as Not sensitive as the benchmark level.

The southern-most distribution of Urospora penicilliformis in the northern Hemisphere is limited by the 26°S and 16°W isotherm (Bischoff & Wiencke, 1995). Samples of Urospora penicilliformis were grown in the laboratory for two weeks at a range of temperatures. Cold temperate samples in the Northern Hemisphere grew between 0-20°C and survived up to 25-26°C. Arctic strains survive up to 23-24°C while Antarctic strains survive up to 19°C (Bischoff & Wiencke, 1995).

This biotope is characteristic of the littoral fringe, where it is rarely inundated, but exposed to direct sunlight for prolonged periods, warm weather in summer and frost and ice in winter. Urospora sp. are most abundant in winter to spring and sometimes summer, while Ulothrix is most abundant in summer so that increases in temperature may change to the relative abundance of the species within the biotope.  However, the temperature will also affect water retention and desiccation, so that the effect of temperature change will also vary depending on the wave exposure, splash, and spray, humidity and cloud cover.  Nevertheless, the wide distribution of both species in the North Hemisphere suggests that the biotope is resistant of temperature change at the benchmark level.  Therefore, resistance is probably High, resilience is High (by default) and the biotope is assessed as Not sensitive as the benchmark level.

The marine Ulothrix species in the British Isles are recorded as tufts and mats on mud, artificial and other hard substrata, in saltmarshes, from the mid-littoral to littoral fringe and supralittoral pools. They flourish in areas of extreme salinity variation and occur close to the mouth of freshwater streams or rocks in freshwater seeps (Brodie et al., 2007).  The brackish-water Ulothrix flacca is only rarely recorded in freshwater (Brodie et al., 2007).  Hanic (1965 cited in Burrows. 1991) noted that the dwarf form of Urospora wormskioldii predominated at high (50‰) and low (10‰) salinities while the filamentous predominated at 20-30‰.

The littoral fringe is probably exposed to a wide range of salinities due to the evaporation of seawater from splash and spray, and direct rainfall or freshwater runoff.  Therefore, the biotope is likely to be resistant of changes in salinity.  The occurrence of the characteristic species in supralittoral pools also suggests they could resist hypersaline conditions. Therefore, a resistance of High is suggested. Hence, resilience is High, so that the biotope is probably Not sensitive.

The marine Ulothrix species in the British Isles are recorded as tufts and mats on mud, artificial and other hard substrata, in saltmarshes, from the mid-littoral to littoral fringe and supralittoral pools. They flourish in areas of extreme salinity variation and occur close to the mouth of freshwater streams or rocks in freshwater seeps (Brodie et al., 2007).  The brackish-water Ulothrix flacca is only rarely recorded in freshwater (Brodie et al., 2007).  Hanic (1965 cited in Burrows. 1991) noted that the dwarf form of Urospora wormskioldii predominated at high (50‰) and low (10‰) salinities while the filamentous predominated at 20-30‰.

The littoral fringe is probably exposed to a wide range of salinities due to the evaporation of seawater from splash and spray, and direct rainfall or freshwater runoff.  Therefore, the biotope is likely to be resistant of changes in salinity.  The occurrence of the characteristic species on freshwater seeps and in brackish conditions also suggests they could resist hyposaline conditions. Therefore, a resistance of High is suggested. Hence, resilience is High, so that the biotope is probably Not sensitive.

The littoral fringe is unlikely to be affected by changes in water flow as described in the pressure benchmark. Runoff due to heavy rainfall is possible but is outside the scope of the pressure. Therefore, the pressure is Not relevant.

Water retention and wetting are probably vital to the survival of this biotope where wave action supplies the water to the littoral fringe in the form of wave splash and spray. The vertical extent of the biotope is probably determined by wave action (via spray and splash) and in turn the emergence regime.  A decrease in emergence regime is likely to result in competition from macroalgae resulting in loss of extent, especially in no other suitable substratum is available. Conversely, an increase in emergence will probably result in the biotope moving further down the shore.  Therefore, a resistance of Low is recorded. As resilience is probably High, sensitivity is assessed as Low.

Water retention and wetting are probably vital to the survival of this biotope where wave action supplies the water to the littoral fringe in the form of wave splash and spray. The vertical extent of the biotope is probably determined by wave action (via spray and splash).  For example, Fletcher (1980b) noted that the vertical height of the green algal band on  artificial substrata (pontoons) in Langstone harbour was greater in areas subject to wave exposure when compared to the sheltered inner reaches of the harbour.  Therefore, a decrease in wave exposure is likely to reduce the vertical extent of the biotope, while an increase in wave exposure may increase its extent, depending on competition from other green algae.  However, a 3-5% change in significant wave height is unlikely to be significant in wave exposed conditions. Therefore, the biotope is probably Not sensitive (resistance and resilience are High) at the benchmark level.

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

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

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

No evidence found.

This pressure is Not assessed.

The littoral fringe is is rarely inundated and this biotope is probably exposed to the air for the majority of the time. Even if the water lapping over the littoral fringe was deoxygenated, wave action and turbulent flow over the rock surface would probably aerate the water column. Hence, the biotope is unlikely to be exposed to deoxygenated conditions. 

Fletcher (1996) listed Urospora penicilliformis as a species characteristic of eutrophic waters.  Therefore, the biotope might benefit from eutrophication. However, this biotope is considered to be Not sensitive at the pressure benchmark that assumes compliance with good status as defined by the WFD.

Opportunistic green algae are reported to flourish in nutrient enriched conditions (Fletcher, 1996). Organic enrichment will result in the release of nutrients due to bacterial decomposition and, so, may lead to an increase in green algal cover.  Organic enrichment may occur on cliffs due to runoff from agricultural land and may benefit the biotope.  Therefore, the biotope is considered to be Not sensitive (resistance and resilience are High).

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

Ulothrix and Urospora species can occur on saltmarsh plants, on mud and on artificial substrata (Brodie et al., 2007). However, this biotope is characteristic of hard rock or soft rock (chalk) substrata. A change to a sedimentary substratum, however unlikely, would result in the permanent loss of the biotope. Therefore, the biotope has a resistance of None, with a Very low resilience (as the effect is permanent) and, therefore, a sensitivity of High. Although no specific evidence is described confidence in this assessment is ‘High’, due to the incontrovertible nature of this pressure.

Ulothrix and Urospora species can occur on saltmarsh plants, on mud and on artificial substrata (Brodie et al., 2007). However, this biotope is characteristic of hard rock or soft rock (chalk) substrata. Therefore, a change in sediment type is Not relevant.

This biotope is characteristic of hard rock or soft rock (chalk) substrata. Removal of  the substratum is not relevant where the biotope occurs on hard bedrock. However, chalk habitats can be subject to landslides but also direct extraction as a result of tunnelling or other construction activities. Removal of the substrata would remove the biotope from the affected area. Therefore, a resistance of None is recorded. However, where suitable habitat remains (e.g chalk or hard rock surface) or where artificial hard substrata are introduced, the characteristic species could colonize the habitat quickly, and resilience is probably High. Therefore, sensitivity is assessed as Medium.

This biotope is probably overlooked and included under 'green algae', therefore, little direct evidence on the effect of abrasion was found.  The characteristic species are probably a component of the 'green algae' regularly cleaned from jetties, pontoons, and slipways. In experimental trampling studies, Fletcher & Frid (1996a&b) noted that the abundance of Ulva spp. (as Enteromorpha) was routinely greater in trampled rather than untrampled areas. This suggested that opportunistic algae were able to colonize the bare space created by trampling, and benefited from the reduced abundance of other macroalgae.  Overall, Ulothrix sp. and Urospora sp. are not physically robust and are probably removed easily from the rock surface, except in cracks and fissures protected from abrasion, so the resistance is probably Low.  Vertical surfaces are probably protected from trampling except in areas subject to climbing.  However, resilience is probably High and sensitivity is assessed as Low.

Penetration of hard rock (as described by the pressure definition) is 'Not relevant'.  However, soft rock may be tunnelled into or removed by construction activities. Removal of the rock surface would result in loss of the biotope from the affected area.  Therefore, resistance is assessed as Low.  As resilience is likely to be High sensitivity is assessed as Low.

The littoral fringe or supralittoral are rarely inundated. It is, therefore, unlikely to be exposed to changes in water clarity due to changes in suspended sediment.

Smothering could occur as a result of rainwater runoff of silt and soil from the tops of the cliffs. However, where the biotope occurs on vertical or steep cliffs the slope would preclude the build up of significant deposits (except on crevices and pits) sufficient to block the algal communities access to sunlight.  Therefore, the factor is probably Not relevant at the level of the benchmark. Smothering by impermeable materials or by other hard construction materials, however, would result in loss of the biotope (see physical loss above).

Smothering could occur as a result of rainwater runoff of silt and soil from the tops of the cliffs. However, where the biotope occured on vertical or steep cliffs the slope would preclude the build up of significant deposits (except on crevices and pits) sufficient to block the algal communities access to sunlight.  Therefore, the factor is probably Not relevant at the level of the benchmark. Smothering by impermeable materials or by other hard construction materials, however, would result in loss of the biotope (see physical loss above).

Not assessed.

No evidence was found.

Not relevant.  The biotope is rarely underwater and macroalgae are not known to respond to noise.

The littoral fringe is rarely submerged. Therefore, the species that characterize this biotope are probably adapted to prolonged exposure to sunlight, and unlikely to be affected by introduced artificial light. Roleda et al. (2009a&b) reported that Urospora penicilliformis was insensitive to the effects of natural and artificial ultraviolet light (UV) and could cope with the high UV found in cold-temperate waters of both hemispheres and increases in UV due to a reduction in the ozone layer in polar regions. No evidence on the effects of shading was found. However, its presence in exposed cliff faces suggests that it may be out-competed in shaded areas. Therefore, a resistance of Medium is suggested, with Low confidence. Resilience is likely to be High so that sensitivity is assessed a Low.

Not relevant. This pressure is considered applicable to mobile species, e.g. fish and marine mammals rather than seabed habitats. Physical and hydrographic barriers may limit the dispersal of spores. But spore dispersal is not considered under the pressure definition and benchmark.

The pressure definition is not directly applicable to the littoral fringe so Not relevant has been recorded.  Collision via ship groundings or terrestrial vehicles is possible but the effects are probably similar to those of abrasion above.

Not relevant. Macroalgae respond to light intensity but are unlikely to respond to 'visual' cues.

No evidence of the translocation, breeding or species hybridization was found.

No evidence was found.

No evidence on disease or pathogens mediated mortality was found.

The algal community characteristic of this biotope is unlikely to be targetted by any commercial or recreational fishery or harvest.

Incidental removal of the algal mat would probably remove the entire belt rather than specific characteristic species. Where present, mobile invertebrate fauna are probably not entirely dependent on the 'belt' for food or habitat and would forage elsewhere.  However, this algal community is unlikely to be targetted by any commercial or recreational fishery or harvest. Accidental physical disturbance due to access (e.g. trampling) or grounding is examined under abrasion above.