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Indicator Assessment
In 2012, the concentrations of the eight assessed hazardous substances were generally: Low or Moderate for Hexachlorobenzene (HCB) and lindane; Moderate for cadmium, mercury, lead, dichlorodiphenyltrichloroethane (DDT) and 6-Benzylaminopurine BAP; and Moderate or High for polychlorinated biphenyl (PCB).
A general downward trend was found between 2003 and 2012 in the North-East Atlantic for cadmium, lead, lindane, PCB, DDT and BAP, and also in the Baltic Sea for lindane and PCB. No trends could be calculated for the other regional seas.
Hazardous substances in marine organisms in European seas
Note: This figure shows the 2012 aggregated assessment for 8 hazardous substances (or groups) in marine organisms in regional seas around Europe. It consists of eight maps showing available data for the Northeast Atlantic ocean, Baltic sea, Black Sea and Mediterranean sea; one map for each substance. Each map shows the locations where the substance was measured, and coloured to indicate which class was registered; green (Low concentration), yellow (Moderate concentration) or red (High concentration). In addition a pie chart is presented on the map showing the percent of each class within each of the four regional seas. Furthermore, any regional trend observed between 2003-2012 for a particular class is indicated by an arrow.
This indicator covers the North-East Atlantic, the Baltic Sea, the Mediterranean Sea and the Black Sea. The assessment results show that concentrations are generally Low or Moderate for all eight hazardous substances (Figure 1).
Cadmium, lead and mercury are found at low concentrations in the Earth's crust and occur naturally in seawater. HCB, lindane, PCB and DDT are synthetic substances that are not found naturally in the environment. The polycyclic aromatic hydrocarbon (PAH) compound benzo(a)pyrene occurs naturally but, as with the other contaminants, human activities have caused a general mobilisation of these hazardous substances that can result in harmful effects in aquatic and terrestrial environments. In the marine environment, they accumulate in fish and shell fish, and because these, in return, are a food source for marine wildlife and humans the substances are moved to higher levels in the food chain. The contaminants are not needed for any organism (they are not essential) and are toxic. In humans long-term exposure or consumption of contaminated seafoods can be detrimental. For this reason seven of the eight chemicals have been banned from use (only BAP is not banned). The main sources, at least in the North Sea, are from general waste/disposal, burning of fossil fuels and industrial activities (NSC, 2002), including mining and production. The EEA has published a more thorough description of their sources and dangers to the environment (EEA 2011).
This assessment is based on data reported to the EEA by EEA member countries where there are some issues with data availability and quality. The assessment therefore does not necessarily convey the uncertainty these problems cause. It also should be noted that the three-class system applied for assessing the concentrations of hazardous substances does not necessarily highlight where there is a risk to human consumption.
The key assessment can be summarised as follows:
The decrease in inputs to the North-East Atlantic since 1990 (EEA 2011) is reflected in the general decrease in concentrations for seven of the eight contaminants (i.e., cadmium, lead, HCB, lindane, DDT, PCB and BAP) in mussels and fish in this region, 2003-2012. This indicates that the measures and initiatives to reduce the input of these substances and to protect the marine environment are of some success.
Abatement policies have also been in effect for the Baltic Sea and concentrations have, in general, decreased for lindane and PCB during the period 2003 to 2012. This indicated that abatement policies in this region were of some success.
The assessment of the Mediterranean is based on contributions from four countries: Croatia, France, Italy and Slovenia. Policies to reduce pollution have been in effect here but no general regional trend was detected. An improvement in data reporting is needed to provide a better estimate of levels and trends for this sea.
Data for the Black Sea concerned only concentrations of cadmium, lead, HCB and lindane in mussels from four stations in Romania. Concentrations were Moderate to High. No trends were discerned.
CADMIUM
Assessment of sub-indicator:
Summary: Concentrations of cadmium in recent years were generally classified as Moderate in mussels and fish of the North-East Atlantic, fish in the Baltic Sea, and mussels in the Mediterranean Sea and Black Sea. A general downward regional trend was detected in the North-East Atlantic, which gives some indication that conditions are improving (assessment based on results for 2003-2012).
Cadmium is primarily produced as a byproduct of the extraction, smelting and refining of zinc and other non-ferrous metals (EEA, 2011). The main sources, at least in the North Sea, are from general waste/disposal and industrial activities (NSC, 2002). Sources of the metal in the environment include mining and production, the metal (including steel) and coating/electroplating industries, the production and deposition of nickel-cadmium batteries, the burning of fossil fuels, the use of phosphate fertilisers, waste incineration, leaching from waste deposits and, finally, the use of cadmium salts as a stabiliser and/or colouring agent.
Cadmium is widely present at Low concentrations in the Earth's crust, but human activities have caused a general mobilisation of the metal in aquatic and terrestrial environments. Elevated levels of cadmium can be found in the sediment in estuarine and coastal waters of the Baltic Sea (HELCOM, 2010) and the North Sea (OSPAR, 2010). Re-suspension of hazardous substances can occur if sediments are disturbed or displaced by, for example, dredging (OSPAR 2009). There is also evidence of significant atmospheric transport (OSPAR, 2004).
It is not needed for any organism (it is not essential) and the metal is highly toxic. The metal affects vital biological processes such as ion exchange, energy production and protein synthesis, mainly through interaction with the metabolism of essential trace metals such as zinc and calcium. In marine ecosystems, some seabird species (eating contaminated mussels) have been identified as possibly the most sensitive component through secondary poisoning (OSPAR 1996, 2004). Due to its environmental toxicity and threat to human health, cadmium is classified as a Priority Hazardous Substance under the Environmental Quality Standards Directive (2008/105/EC), which requires that all discharges, emissions and losses cease over time.
The station-by-station overview of 2003-2012 concentrations of cadmium for mussels (both Mytilus edulis and M. galloprovincialis) indicated that concentrations were generally Moderate and to a lesser degree Low. Elevated concentrations were often associated with estuaries for large rivers, in areas with point discharges (e.g. Sørfjord, western Norway) and in some harbours. The areas from which mussels did not appear to be suitable for human consumption were found in 10 cases in France, Denmark, Norway, the Netherlands, the United Kingdom and Romania (Figure 1).
312 temporal trends - 286 for mussels and 26 for fish - were statistically analysed on a station-by-station basis, out of a total of 406 datasets. Of these, only 69 (22.1%) were significant, 48 downwards and 21 upwards. Inputs have been decreasing in the North-East Atlantic (cf. EEA 2011). The regional assessment for this region indicated a general statistically significant downward trend. Moderate concentrations are in general decreasing for this region (Figure 1). Concentrations in one area with High concentrations (Sørfjord, Norway) are decreasing. Considering all classes, most downward trends were found in Norway as well as Ireland and the United Kingdom.
MERCURY
Assessment of sub-indicator:
Summary: Concentrations of mercury in recent years were generally classified as Moderate in mussels and fish of the North-East Atlantic and the Baltic Sea, and mussels in the Mediterranean. There is a majority of upward trends in the North-East Atlantic (assessment based on results for 2003-2012).
The main anthropogenic sources of mercury are from general waste/disposal and industrial activities (EEA, 2011). It is still used in various products, e.g. batteries and electronics. Furthermore, low quantities in fossil fuels and municipal waste ensure continued emissions of mercury into the atmosphere. Mercury is subject to long-range transboundary transport (EEA, 2011). It has no known biological function. It is highly toxic and is considered one of the most dangerous metals in the aquatic environment due to it's toxicity and potential for bioaccumulation/biomagnification, particularly under anoxic conditions, which favour the transformation of inorganic mercury into organic forms. Organic forms of mercury affect the nervous system, whereas the inorganic forms affect a range of cellular processes.
In marine ecosystems, organisms at the top of food chains, mainly seabirds and marine mammals have been identified as being most sensitive (through secondary poisoning) (OSPAR 2004). Mercury, as well as DDT (discussed below), is shown to be a major culprit for the decline in populations of predatory birds in the '60s and '70s. These populations have since recovered mainly because of restrictions on the discharge of mercury and the banning of DDT. There is a continuous microbial transformation of inorganic to organic mercury in the aquatic environment and mercury in, for example, fish is nearly all organic mercury. Methyl mercury is one of the few environmental contaminants that has been established as embryotoxic to humans.
Elevated levels of mercury can be found in the sediment in estuarine and coastal waters of the Baltic Sea (HELCOM, 2010) and North Sea (OSPAR, 2010). Re-suspension of hazardous substances can occur if sediments are disturbed or displaced by, for example, dredging (OSPAR 2009). The Polar Regions are affected by long-range transported mercury, and the concentration in some marine mammals seems to have increased over the previous two decades (AMAP, 2011). The Arctic marine food web is often in focus regarding the risk of mercury to ecosystems. It is, however, important to acknowledge that the impacts of mercury are not only restricted to the Polar Regions. In warmer waters, predatory marine mammals may also be exposed to mercury levels that threaten health.
Due to its environmental toxicity and threat to human health, mercury is classified as a Priority Hazardous Substance under the Environmental Quality Standards Directive (2013/39/EU), which requires that all discharges, emissions and losses cease over time.
The station-by-station overview of 2003-2012 concentrations of mercury for mussels (both Mytilus edulis and M. galloprovincialis) and fish indicated that concentrations were generally Moderate and, to a lesser degree, Low. High concentrations, i.e. concentrations that are not suitable for human consumption, were found in seven cases for mussels (six in areas of Italy and one station in Croatia) and three cases for fish (Denmark, United Kingdom and Norway).
401 temporal trends - 330 for mussels, 71 for fish - were statistically analysed on a station-by-station basis, out of a total of 501 datasets. of these, only 63 (15.7%) were significant, 32 down and 31 up (Figure 1). Inputs to the North-East Atlantic have remained about 50% below the 1990 average since 1995 (cf. EEA 2011). No statistically significant general trend was found for any region, however, an upward trend was found for Moderate concentrations in the Mediterranean Sea (Figure 1). Most downward trends (regardless of class) were found in the United Kingdom and Norway. Most upward trends were found only in the United Kingdom, Denmark and Norway. The one station with High concentrations and an upward trend was in the Netherlands.
LEAD
Assessment of sub-indicator:
Summary:
Concentrations of lead in recent years were generally classified as Moderate in mussels and fish of the North-East Atlantic, Baltic Sea, the Mediterranean Sea and the Black Sea. A regional downward trend was found for the North-East Atlantic (assessment based on results for 2003-2012).
Lead is widely distributed in the crust of the Earth, most commonly found with deposits of other metals like zinc, cadmium, silver and copper. The main anthropogenic sources are from general waste/disposal and industrial activities (NSC, 2002). There is evidence of significant atmospheric transport (OSPAR, 2004). Lead is non-essential and toxic. Lead has a high affinity for particles and is rarely found in high concentrations in seawater. Some algae are especially sensitive to lead (OSPAR 1996), but lead may affect aquatic species at different trophic levels. In vertebrates, lead predominantly accumulates in bone and blood. Exposure to high concentrations will cause decreased synthesis of hemoglobin and eventually anemia. Severe exposure to inorganic lead may cause encephalopathy and mental retardation. Exposure to high concentrations will also cause decreased synthesis of haemoglobin and eventually anaemia.
The station-by-station overview of 2003-2012 concentrations of lead for mussels (both Mytilus edulis and M. galloprovincialis) and fish indicated that concentrations were generally Moderate and to a lesser degree Low for the North-East Atlantic, the Baltic, Mediterranean and Black seas. (Figure 1). High concentrations, i.e. concentrations that are not suitable for human consumption, were found mainly along the North-West coast of Italy, Sardinia and the Spanish coast of the Bay of Biscay.
346 temporal trends - 333 for mussels, 13 for fish - were statistically analysed on station-by-station basis, out of 457 datasets. Of these, 63 (18.2%) were significant, 46 downwards and 17 upwards. Inputs have been decreasing in the North-East Atlantic (cf. EEA 2011). This is reflected in the general downward trend for mussels and fish for this region. Low and Moderate concentrations in the North-East Atlantic are, in general, decreasing (Figure 1). Upward trends were found where there were High concentrations at three stations in Italy as well as a station in Denmark.
HCB
Assessment of sub-indicator:
Summary:
Concentrations of HCB in recent years were generally classified as Low or Moderate in the North-East Atlantic, the Baltic Sea and the Mediterranean Sea. A general regional trend downwards was detected in the North-East Atlantic, which gives some indication that conditions are improving (assessment based on results for 2003-2012).
HCB (hexachlorobenzene) is formed as a by-product, impurity, or intermediate in various manufacturing processes, including the production of chlorinated solvents and pesticides. HCB is also formed as a product of incomplete combustion in a variety of combustion and incineration processes. Control of HCB is hampered by its long range atmospheric transport from other regions. It was used as a biocide until 1965. Chronic exposure can be a health risk to humans. Persistent organic contaminants (e.g. HCB, lindane, PCBs and DDT) have low water solubility, high lipophilicity and are resistant to biodegradation. These properties lead to uptake and accumulation in the fatty tissues of living organisms, in some instances causing biomagnification through food chains. The highest concentrations of organic contaminants are, therefore, found in top predators, such as sea birds, marine mammals and polar bear (Bernhoft et al. 1997; Ruus et al. 2002). Adverse effects may comprise disruption of the immune system, disruption of hormone production or transport, impairment of reproduction, embryonic damage, cancer, or damage to the nerve system.
The station-by-station overview of 2003-2012 concentrations of HCB (hexachlorobenzene) for mussels (both Mytilus edulis and M. galloprovincialis) indicated that concentrations were generally Low or Moderate (Figure 1). High concentrations were found at 10 mussel stations (one in Italy, three on the North coast of Spain, three in the United Kingdom and three in Romania). High concentrations were also found at two fish stations (Norway and Estonia).
159 temporal trends - 118 for mussels, 41 for fish - statistically analysed on a station-by-station basis, out of 253 datasets. Of these, 20 (12.6%) were significant, 17 down and three up (Figure 1). A regional downward trend was found for the North-East Atlantic. Moderate concentrations in this region are decreasing (Figure 1). Only three upward trends were found; two in the Low class and one in the Moderate class. Considering that concentrations are generally Low or Moderate in the Mediterranean, the Baltic Sea and North-East Atlantic, the predominance of no trends or downward trends is a positive signal.
LINDANE
Assessment of sub-indicator:
Summary:
Concentrations of lindane in recent years were generally classified as Low or Moderate in the North-East Atlantic, the Baltic Sea and the Mediterranean. Regional downward trends were found in the North-East Atlantic and the Baltic Sea which are positive signs (assessment based on results for 2003-2012).
Lindane or HCH (1,2,3,4,5,6-hexachlorocyclohexane), also known as benzenehexachloride (BHC), is a pesticide that is still used in parts of the world. Non-agricultural use of lindane includes use for wood preservation, as an insecticide, as rodenticide and for medicinal purposes (scab and louse ointments). Lindane is an irritant in humans and may affect mucus membranes, immune and nervous systems following exposure. Lindane is present in high concentrations in the fat of Arctic seals and polar bears.
From the limited data available on acute and chronic toxicity, some crustacean species appear to be particularly sensitive to lindane (and of course insects in freshwater), whereas e.g. molluscs and algae do not appear to be very sensitive (OSPAR 1996, 2004). In addition to the general adverse effects related to persistent organic contaminants (cf. see text for HCB), lindane is also present in high concentrations in the fat of Arctic mammals (seals, polar bears).
The station-by-station overview of 2003-2012 concentrations of lindane (gamma HCH) for mussels (both Mytilus edulis and M. galloprovincialis) and fish indicated that concentrations were predominantly Low in the North-East Atlantic and the Mediterranean Sea and Moderate in the Baltic Sea (Figure 1). High concentrations in mussels were generally found on the Italian west coast and secondarily the north coast of Spain and Brittany.
156 temporal trends - 125 for mussels, 31 for fish - were statistically analysed on a station-by-station basis, out of 253 datasets. Of these, 72 (46.2%) were significant, 68 downwards and 4 upwards (Figure 1). Inputs have been decreasing in the North-East Atlantic (cf. EEA 2011). Regional trend analysis indicated a general decrease in lindane in the North-East Atlantic as well as in the Baltic Sea. Low and Moderate concentrations in the North-East Atlantic are, in general, decreasing (Figure 1). The four stations with upwards trends were located on the Spanish coast of the Bay of Biscay; all of these with Low concentrations.
PCB
Assessment of sub-indicator:
Summary:
Concentrations of PCB in recent years were generally classified as Moderate or Low in the North-East Atlantic, Baltic Sea and the Mediterranean Sea. Regional downward trends were found in the North-East Atlantic and the Baltic Sea which are positive signs (assessment based on results for 2003-2012).
Polychlorinated biphenyls (PCBs) are a group of theoretically 209 different compounds (congeners) of which 150-160 are found in the environment. It should be noted that the range of PCBs includes very different substances, both with regard to physio-chemical properties and with regard to their biological activity. A distinction is commonly made between the generally more carcinogenic "dioxin-like" PCBs (non- and mono-ortho chlorinated) and the more immunotoxic "bulky" PCBs (chlorinated in ≥2 ortho positions).
All PCBs are man-made, but are now found all over Earth due to their persistence and relative volatility. PCBs have been previously widely used in electrical equipment, and also as a plasticiser and paint additive. In addition to the general adverse effect related to persistent organic contaminants (cf. see text for HCB), PCBs have extreme mobility and the ability to bioaccumulate and magnify in marine food webs, where long-lived animals at high trophic levels appear to be most at risk from PCBs.
As for DDT, PCBs are thought to be involved in the observed reproductive problems of polar bears and possibly earlier morphological aberrations in Baltic seals (namely due to chemical pollution from the river Rhine in the 1980s; Reijnders 1986). PCBs have been associated with lymphocyte proliferation in seal pups, which can result in greater susceptibility to infection (Levin et al. 2005). PCBs have potentially endocrine-disrupting properties (EEA, 2011). Furthermore, suppression of immune system function (specifically natural killer cell activity) in seals fed Baltic Sea herring (also highly contaminated with PCBs) has been observed (Ross et al., 1996). There is also an indication of contaminant-associated suppression of antibody-mediated immunity in polar bears (Bernhoft et al., 2000).
The station-by-station overview of 2003-2012 concentrations of PCB (sum of congeners 28, 52, 101, 118, 138, 153 and 180) for mussels (both Mytilus edulis and M. galloprovincialis) and fish indicated that concentrations were generally Moderate or Low (Figure 1). Less than 8% of the stations had Low concentrations. High concentrations were found in every country that submitted data except Estonia, Croatia, Slovenia, Poland and Romania. It should be noted that High concentrations do not necessarily mean a risk to human health.
319 temporal trends - 250 for mussels, 69 for fish - were statistically analysed on a station-by-station basis, out of 404 datasets. Of these, 59 (18.5%) were significant, 45 downwards and 14 upwards (Figure 1). Inputs have been decreasing in the North-East Atlantic (cf. EEA 2011). Regional trend analysis indicated a general decrease in PCB in the North-East Atlantic as well as in the Baltic Sea. Moderate concentrations for these two regions are decreasing, however High concentrations in the Mediterranean are in general increasing (Figure 1). The 42 downward trends where High or Moderate concentrations were registered at stations in France, Denmark, Estonia, the United Kingdom, Ireland, Italy, the Netherlands, Norway, Poland and Sweden. Ten of the eleven upward trends where High concentrations were registered were found in Italy.
DDT
Assessment of sub-indicator:
Summary:
Concentrations of DDT in recent years were predominantly classified as Moderate in the North-East Atlantic, Baltic Sea and the Mediterranean Sea. A general regional trend downwards was detected in the North-East Atlantic, which gives some indication that conditions are improving (assessment based on results for 2003-2012).
DDT (dichlorodiphenyltrichloroethane) is a synthetic organochlorine insecticide that was first used to control insects that were vectors for human diseases at the end of World War II. After the war, it found a ready market in peacetime agricultural enterprise. All use of DDT was discontinued in western European countries around 1990, although heavy use was banned two decades earlier. However, in developing countries, the need for cheap insecticides (to control mosquitoes, and hence malaria) has kept DDT in use also in later years. Furthermore, in some areas, e.g. in fruit-growing areas in western Norway, there are recent inputs of DDT, probably due to leaching from buried waste or unused canisters. In addition, there is continued leaching from soil and river sediments in some areas.
DDT has, over the past 50-60 years, been spread over the entire globe and is now found in all natural waters and organisms. In addition to the general adverse effects related to persistent organic contaminants (cf. see text for HCB), DDT and its derivates have been found responsible for eggshell thinning and consequent decline in populations of predatory birds in ‘60s and ‘70s, a situation that has since has improved, in part due the banning of DDT. There is also evidence that a metabolite of DDT (p,p’-DDE) may have consequences for the reproduction of marine animals by affecting testosterone levels (Subramanian et al. 1987).
The station-by-station overview of 2003-2012 concentrations of DDT (using pp'DDE as a surrogate for DDT) for mussels (both Mytilus edulis and M. galloprovincialis) and fish indicated that concentrations were generally Moderate (Figure 1). Less than 9% of the stations had Low concentrations. High concentrations were found in every country that submitted data except Estonia, Finland, Croatia and Romania. It should be noted that High concentrations do not necessarily mean a risk to human health.
214 temporal trends - 179 for mussels, 35 for fish - were statistically analysed on a station-by-station basis out of 274 datasets. of these, 33 (15.4%) were significant, 24 down and 9 up (Figure 1). The regional trend for the North-East Atlantic indicated a general decrease. Moderate concentrations in this region are decreasing (Figure 1). Six of the eight stations with High concentrations and upwards trends were located on the West coast of Italy, the other two in a fjord on the West coast of Norway.
Benzo[a]pyrene (BAP)
Assessment of sub-indicator:
Summary: Concentrations of benzo[a]pyrene (BAP) in recent years were generally classified as Moderate in the North-East Atlantic, Baltic Sea and Mediterranean Sea. Generally there was a predominance of downward trends over upward trends and a regional downward trend was found in the North-East Atlantic (assessment based on results for 2003-2012).
Benzo[a]pyrene (BAP) is a polycyclic aromatic hydrocarbon (PAH). Its metabolites are mutagenic and highly carcinogenic. It occurs naturally but concentrations can be excessive due to anthropogenic activities. Emissions to the atmosphere are far greater than other discharges. Hence, emission reduction measures need to focus upon combustion processes, including those related to the transport sector as well as coal- and wood-powered heating and electricity-generating plants (EEA 2011).
The station-by-station overview of BAP for mussels (both Mytilus edulis and M. galloprovincialis) indicated that concentrations were generally Moderate (Figure 1). Less than 3% of the stations had Low concentrations. The two stations with High concentrations were found in Spain and Norway. It should be noted that High concentrations do not necessarily mean a risk to human health.
113 temporal trends - all for mussels - were statistically analysed on a station-by-station basis, out of a total of 169. of these, only 17 (15.0%) were significant, 14 downwards and 3 upwards (Figure 1). The general trend in the North-East Atlantic is downward. Moderate concentrations in this region are decreasing (Figure 1).
2013/39/EC. Directive 2013/39/EU of the European Parliament and of the Council of 12 August 2013 amending Directives 2000/60/EC and 2008/105/EC as regards priority substances in the field of water policy.
This indicator describes the levels and trends in European seas of concentrations of eight hazardous substances in marine biota, based on the individual assessment of monitoring data for the following substances:
The indicator is based on data for substances measured in organisms from the regional seas as follows:
The classification in the maps is based on concentrations in µg/kg, which are then classified into one of three classes: green (Low concentration), yellow (Moderate concentration) or red (High concentration). In addition a pie chart is presented showing the percentage of each class within each of the four regional seas.
A range of EU, regional and national legislation has been implemented in Europe to address the use of chemicals and their emission to the environment, including fresh and marine waters. The regulation of chemical pollutants in water began with the Dangerous Substances Directive (76/464/EEC), which has been integrated into the Water Framework Directive (2000/60/EC). The WFD represents the single most important piece of EU legislation relating to the quality of fresh, transitional and coastal waters, which aims to attain good ecological and chemical status of these waters by 2015. It requires the establishment of a list of priority substances (Decision 2455/2001/EC gave way to the First list of priority substances), to be selected from amongst those presenting a significant risk to or via the aquatic environment at EU level. It also requires the designation of a subset of priority hazardous substances, and proposals for controls to reduce the emissions, discharges and losses of all the substances and to phase out the emissions, discharges and losses of the subset of priority hazardous substances.
The chemical status of Europe's surface waters is currently addressed by the Environmental Quality Standards Directive – EQSD (2008/105/EC), a 'daughter' directive of the WFD, whose Annex II has replaced the first list of priority substances set out in the Decision 2455/2001/EC. The EQSD defines environmental quality standards (EQSs) in fresh and coastal waters for pollutants of EU-wide relevance known as priority substances (PSs). Member States are required to take actions to meet the quality standards in the EQSD by 2015.
Furthermore, emissions of hazardous chemicals from industrial installations and agricultural activities are regulated in the EU through the Integrated Pollution Prevention and Control (IPPC) Directive, whose abatement measures have contributed to a decline in metal emissions to water and air. Of relevance is also the EC Regulation 1907/2006 on the Registration, Evaluation, Authorisation and Restriction of Chemicals (REACH), which aims to improve the protection of human health and the environment from the risks of chemicals. REACH gives greater responsibility to industry to manage the risks from chemicals and to provide safety information on substances used.
More recently combating this type of pollution in the open sea has been addressed by the Marine Strategy Framework Directive (2008/56/EC), which requires the achievement or maintenance of good environmental status in European seas by the year 2020 at the latest, through the adoption of national marine stategies based on 11 qualitative descriptors. Descriptor 8 (“Concentrations of contaminants are at levels not giving rise to pollution effects”) and Descriptor 9 (“Contaminants in fish and other seafood for human consumption do not exceed levels established by Community legislation or other relevant standards”) refer specifically to contaminants.
The EQSD list of priority substances includes cadmium, mercury, lead, hexachlorobenzene (HCB), lindane and DDT and benzo(a)pyrene, but not PCB. The WFD EQSD was revised in 2013 and the number of hazardous substances listed has increased from 33 to 45. Except for HCB, these substances are also on the list of chemicals for priority action for the OSPAR Marine Convention (OSPAR 1998).
The production and use of DDT, HCB, lindane and PCBs are banned or voluntarily withdrawn within Europe. However, for PCBs, use is still permitted in closed system equipment, manufactured before the ban, until the end of service. Sales to consumers of nickel-cadmium batteries have been banned in Europe.
At a regional level, international regional sea conventions (OSPAR, HELCOM, Barcelona Convention and Black Sea Convention) are also addressing pollution due to hazardous substances in European marine waters.
Article 5 of the revised Helsinki Convention of 1992 requires that the Contracting Parties undertake to prevent and eliminate pollution of the marine environment of the Baltic Sea area caused by harmful substances from all sources (HELCOM 2008). Under this convention, DDT and PCBs are banned and there is agreement that every contracting party shall endeavour to minimise and, whenever possible, to ban the use of cadmium, lead and mecury compounds. HELCOM has also Recommendation 31E/1, adopted May 2010, that Contracting Parties apply the Strategy to implement the HELCOM Objective for hazardous substances, and make use of the principles and methodologies contained therein to move towards the target of the cessation of discharges, emissions and losses of hazardous substances to achieve the Baltic Sea in good environmental status by 2021.
Parties to the Convention for the protection of the Mediterranean Sea against Pollution have identified contaminants or groups of contaminants whose dumping or land-based discharges are prohibited or limited (Barcelona Convention and protocols). Parties to the Convention on the Protection of the Black Sea against Pollution have identified similar groups of contaminants and have protocols to reduce pollution by these harmful substances. However, it should be noted that even though relatively high contamination levels of some pesticides, heavy metals and PCBs are present, these substances are not monitored routinely (BSC 2009).
Complementing these efforts are the Basel, Rotterdam and Stockholm Conventions - multilateral environmental agreements, which share the common objective of protecting human health and the environment from hazardous chemicals and wastes. The Basel Convention has dealt with control of transboundary movements of hazardous wastes and their disposal since 1989. The Rotterdam Convention text, adopted in 2004, promotes shared responsibility and cooperative efforts among Parties in the international trade of certain hazardous chemicals (which include mercury, HCB, lindane, PCB and DDT) in order to protect human health and the environment and to contribute to the environmentally sound use of those hazardous chemical by, inter alia, providing for a national decision making process on their import and export. The Stockholm Convention, which entered into force in 2004, requires Parties to take measures to eliminate or reduce the release of POPs into the environment for which HCB, lindane, PCB and DDT are addressed.
The aim of the Water Framework Directive is to achieve zero, near zero or background concentrations (more specifically defined in a daughter directive on ecological quality standards, i.e. the EQS-directive 2008/105/EC), depending on the contaminant. This is to be achieved through abatement actions on inputs, with the objective of reaching good ecological and chemical status by 2015 of fresh, transitional and coastal waters. However, the WFD only applies to the transitional and coastal environment. Goals similar to the Water Framework Directive have also been outlined by OSPAR and HELCOM. For the Mediterranean Sea, similar targets have been adopted. The reduction and phasing-out targets are formulated in accordance with related regional and international Conventions and programmes, such as the EU Directives, policies and strategies, and the Stockholm and Basel Conventions. However, similar targets have yet to be formulated for the Black Sea, although discussions are under way.
Within the scope of the Marine Strategy Framework Directive, hazardous substances are the relevant criteria and indicators in marine waters under Descriptor 8 (“Concentrations of contaminants are at levels not giving rise to pollution effects”) and 9 (“Contaminants in fish and other seafood for human consumption do not exceed levels established by Community legislation or other relevant standards”). In this regard, Member States are required to take into account relevant existing environmental targets. This would imply, inter alia, the environmental quality standards set out in the EQSD, since it applies to waters common to both the Water Framework Directive and the Marine Strategy Framework Directive, i.e seaward side of the baseline to the extent of territorial waters. A process is underway to define standards for the listed hazardous substances in biota so that these can apply to the marine and coastal environment.
Data sources and coverage
The data used in this indicator is part of the WISE - State of the Environment (SoE) data, available in Waterbase - TCM (Transitional, Coastal and Marine) waters. Waterbase is the generic name given to the EEA´s database on status, quality and quantity of Europe´s water resources. Waterbase – TCM waters contains data collected both from EEA member countries (i.e. belonging to the EIONET) and from the Regional Seas Conventions through the WISE-SoE TCM data collection process (WISE-SoE was formerly known as Eionet-Water and Eurowaternet). The resulting WISE SoE TCM dataset is therefore made of sub-samples of national data assembled for the purpose of providing comparable indicators of state and impact of transitional, coastal and marine waters on a Europe-wide scale.
Geographical coverage
There is generally good data coverage for concentrations in the North-East Atlantic, except for Portugal, and in the Baltic. The Mediterranean Sea was only represented by data from a few countries. For the Black Sea, the only available data was Romanian mussel data, but because of the requirement for conversion to a preferred basis, too little data was available for the 2013 assessment. However, in the 2014 assessment some stations that were quite close to each other were grouped in order to get the minimum three years of data (see further below), so an assessment could be made.
Temporal coverage
Concentrations in biota were measured during the period 1978 to 2012. Only data from the period starting in 1998 was considered for the trend assessment up to the 2013 assessment. For the latest 2014 assessment, only data from the period starting in 2003 was considered. Furthermore the assessment only includes time series that have data from 2006 or later and that cover at least three years, not necessarily contiguous. Many of these series have gaps, with intervals of two or more years between observations.
Tissues
For fish, only concentrations from the following tissues were used:
Conversion to a preferred basis for data in assessment
The classification by which the data are assessed requires conversion to the preferred basis (OSPAR, 2008). In order to create comparability between data within and between stations, and to allow comparison with assessment criteria, it is necessary to choose the bases on which all concentrations must be expressed. The preferred bases applied by OSPAR (2008) are:
The choice of bases aimed at meeting several considerations: scientific validity, uniformity for groups of contaminants for particular tissues and a minimum loss of data. As to the latter, the choice of bases will affect the amount of data that can be included in the assessment, depending on available information on dry weights, wet weights, lipid weights and the ratio between dry and wet weight. For example, for the Mediterranean Sea, mussel data from Greece could not be converted to the preferred dry-weight basis on a sample-specific basis, and was therefore excluded from the assessment. For the 2014 assessment, data available on dry weight was converted to wet weight basis, but only when a sample-specific dry weight-wet weight ratio was available. An exception was made for data from Mediterranean mussels (Mytilus galloprovincialis) in France and Italy where it assumed the dry weight-wet weight ratio to be 0.19, as used by OSPAR, in order to increase the geographic coverage.
Aggregation of data by station
In a primary step, each time series (combination of location, species, tissue and determinand) is aggregated to a median concentration for each year. For years where some values are reported as ´less-thans´ (below reporting limit) and only 50% or less of the observations are real values above the largest ´less-than´ limit, the median can only be specified as a low-high range. The high limit is the estimate found when using the upper limit for ´less-than´ observations, and the low limit is the median estimate found by assuming 0 for these observations. The low limit will often be 0, but may also be a positive value. If the low and high limit is the same value, the median is well-defined, even if there are some ´less-than´ values in the sample.
Some data series contain concentrations given as exact zero. If this occurs for less than 50% of observations within a year, the high limit for the median of that year will still be a positive value. If more than 50% of observations are reported as 0, the smallest value > 0 is used as the best approximation to the median value. It should be noted that reporting concentrations as exact zero is not correct; it should either be a definite positive value or reported as below a detection limit > 0. The procedure described above implicitly assumes that zero values represent concentrations below the reported positive values or detection limits; if this is not the case the procedure may give a misleading result.
In a secondary step, each resulting time series of median values (or ranges) was assessed separately. Only time series with at least three years of data, of which one year must be 2006 or later, were included in the assessments. Only data from the years 1998-2010 was included in the 2013 analysis whereas the period was 2033-2012 for the 2014 one. Years where all values are reported as equal to zero are excluded from the analysis.
Trend assessment for each time series
The trend assessment method depends on whether all median values are well-defined, or whether some median values can only be specified as ranges.
Time series where all median values are well-defined
For such series, the trend is analysed both by regression on log-transformed medians versus year and by non-parametric Mann-Kendall test.
The regression method depends on the length of the time series:
Both types of regression test are done at a 5% two-tail significance level. Extremely low values that deviate from the trend by more than a factor 10 will be excluded if that results in a lower classification level, see below. In addition to the regression, a non-parametric Mann-Kendall trend test is done also with 5% significance level (ICES, 2000).
The nonparametric Mann-Kendall test is done for all time series with four years or more.
In cases where both regression and Mann-Kendall assessments have been made, the results are combined as follows: If only one of the two methods shows a significant trend, that result is used. If the two methods should both indicate significant trend, but in opposite directions, the series would be flagged as having inconsistent trend indication, however, this does not occur in the present dataset. It is found that the two methods supplement each other: The regression test, in particular the smoother test for series of seven or more years, is better at detecting clear differences in level between the beginning and end of a time series if there are large fluctuations in between (non-monotonic trends). The Mann-Kendall test is better at detecting trends if for instance values are consistently low in the last part of the series, but has large variations in the first part of the time series.
Time series where some median values can only be specified as ranges
Regional trend assessment
The regional trend assessment is based on a tally of significant upward and downward trends and the contaminant-region trend (general trend) or contaminant-region-class trend in question (OSPAR 2009b). The significance of the tendency is determined by using the cumulative binomial distribution probability. This implies an assumption that each trend represents an independent measure of overall trend, which cannot be expected to be met, so the statistical assessment of the regional trend is merely indicative.
Classification of concentrations (i.e. levels) – low, moderate, high
For time series with five or more years of data, the upper 95% confidence limit for the fitted value for the last year in the data series (equal or > 2006) is used to classify environmental status. For time series covering only three or four years of data, the upper 95% confidence limit for the average of the yearly medians is used. The classification is done by comparing the confidence limit to low and high classification levels in Table 1 (see further below). For series with data from only one or two years, no classification is made.
The level is classified as Green if the test value is below the low limit, Yellow if in the low-high classification interval, and Red if it is above the high classification level.
In some series, the normal procedure on the full time series of yearly medians will give unreasonably high assessment levels. In particular, this is the case when there are extreme low values occurring in the series of yearly medians. Such low values will, in many cases, increase the uncertainty estimate so much that the upper 95% confidence level becomes very high, much higher than any observed value. To avoid such unreasonable classification, series where any of the yearly medians are lower than 10% of the fitted value for the same year are reanalysed with such values excluded. If this results in a lower assessment level, the revised analysis is used both for assessment level and time trend. Deviating high yearly medians are never removed, so an extremely high and possibly spurious median for a single year will still increase both fitted value and uncertainty, and may cause very high assessment levels.
It should be noted that classification reflects both observed levels and the uncertainty in trends or levels indicated by data. Thus a Red classification does not necessarily mean that estimated levels are above the limit; it may merely indicate that the uncertainty is so large (because of little data and/or high variability) that it cannot be assessed with reasonable confidence that the true level is below the highest limit.
The regional assessment of current levels is based on a tally of current levels for each of the three categories and for each contaminant and species-tissue in question (OSPAR 2009b). Datasets that are insufficient for trend analyses are weighted by a factor of two. Proportions for different combinations of contaminants and regions are calculated for the categories.
Combined PCB assessment
For PCBs, a combined assessment for each combination of location, species, tissue is made as follows: A significant trend direction (Up/Down) is reported only if at least 50% of all the PCB components where the time trend is assessed (Up/Down/Not significant) has the same significant direction. Missing results (NA for trend ‘test not applied’) do not count; if all components have a trend result NA, that is also the combined result. The combined classification is the next worst classification over the PCB components where a class is specified. NA is also set for time series where it is not possible to assign a direction of change between any two years in the series, no matter how many years the series have. This occurs if all yearly medians given as a specific number are identical, and where all low-high median ranges overlap the ranges and values for all other years. (An example: three years with value 0.1, two years with ranges [0.05-0.2], [0-0.15]). In these cases, it is not possible to define a sensible scale against which to assess the lack of trend indications, and NA seems to be the most relevant classification. NS is reserved for cases where it is possible to assess whether the long-term trend in the time series is significant compared to the short-term (year-to-year) variation.
DDT assessment
For DDT, only the DDE, p,p' component is used for the assessment. The other two frequently measured components are DDD,p,p’ and DDT,p,p’ but they have in generally smaller concentrations than DDE,p,p’. DDE,p,p’ has also been measured in the largest number of samples. In particular DDT,p,p' is missing in a substantial number of samples.
Classification tables
Tables 1 and 2 provide an overview of the concentration limits used in the 2013 and 2014 assessments respectively. Based on those limits, three classes are defined: Low, Moderate and High concentrations. The current EQSD (2013/39/EU) has provisions for eleven substances in biota, including mercury, HCB and benzo(a)pyrene BAP. However, further guidance is needed in order to apply the limits provided by the EQSD, because it is not yet clear how the EQS can be directly applicable to the target tissues used in MAR001 (i.e. liver, fillet or soft body). An EU guidance document in this respect is expected in 2014. Thus limits have been defined based on OSPAR methodology, EU legislation concerning concentrations in relevant foodstuffs (EC no.1881/2006 - only applicable to a few substances relevant for this indicator: cadmium, lead and mercury), or in absence of these, expert judgment is used.
OSPAR has developed Background Assessment Criteria (BAC) and Environmental Assessment Criteria (EAC), which are being applied in this indicator. EACs were preferred over BACs because EACs entail an assessment of harm to the environment, whereas BACs only provide expected concentrations in mussels and fish that have had presumed low exposure to contaminants. Both EAC and EQS are risk based thresholds designed to provide equally good protection of the environment as to the EQSD. Furthermore, there is an ongoing process at OSPAR to harmonise the EACs with the EQS using the same principles for environmental protection. An EQS in the water column calculated from OSPARs EAC does not always agree with the EQS from the directive. One major issue is the choice of assessment factors and biomagnification factors applied. It should also be noted that EAC does not take into account specific long term biological effects such as carcinogenicity, genotoxicity and reproductive disruption and do not include combination toxicity, the assessment criteria in general, and especially for PAHs and PCBs should not be considered final goals or ultimate targets (see OSPAR (2004) for further cautionary notes).
Two different types of EACs were derived. The first type is based on the derived EACs for water or sediment, and transferred to biota using an appropriate bioconcentration bactor (BCF). The second type takes into account that fish or mussels are food for predators. Concentrations in mussels or fish can be derived that protect against this so-called secondary poisoning using appropriate biomagnification factors (BMF). BCF is the ratio of the factor by which the result of the uptake, distribution and elimination of a substance in an organism due to waterborne exposure (EU/ Technical guidance document). Biomagnification is the accumulation and transfer of chemicals via the food chain, resulting in an increase of the internal concentration in organisms at higher levels in the trophic chain (EU/ Technical guidance document) (E.C. 2003).
Substances Species and tissue | Latin name |
Low/ High |
µg/kg | Basis | Reference | Comment |
---|---|---|---|---|---|---|
CADMIUM | ||||||
Mussels |
Mytilus¹sp.
|
Low | 960 | D | OSPAR 2008 | BAC limit |
Mussels |
Mytilus sp.
|
High | 5000 | D | EU 2006 |
Foodstuffs limit for "bivalve molluscs", Regulation (EC) No. 1881/2006, conversion assuming 20% wet weight (cf. OSPAR CEMP assessment manual 2008, Table 2.1)
|
Atlantic cod, liver
|
Gadus Morhua
|
Low | 26 | W | OSPAR 2008 | BAC limit |
Atlantic cod, liver |
Gadus Morhua
|
High | 1000 | W | EU 2006 |
Foodstuffs limit for "bivalve molluscs", Regulation (EC) No. 1881/2006
|
Herring, muscle |
Clupea harengus
|
Low | 26 | W | OSPAR 2008 | BAC limit |
Herring, muscle |
Clupea harengus
|
High | 1000 | W | EU 2006 |
Foodstuffs limit for "bivalve molluscs", Regulation (EC) No. 1881/2006
|
MERCURY | ||||||
Mussels
|
Mytilus¹sp.
|
Low | 90 | D | OSPAR 2008 | BAC limit |
Mussels
|
Mytilus sp.
|
High | 2500 | D | EU 2006 |
Foodstuffs limit for "bivalve molluscs", Regulation (EC) No. 1881/2006, conversion assuming 20% wet weight (cf. OSPAR CEMP assessment manual 2008, Table 2.1)
|
Atlantic cod, muscle
|
Gadus Morhua
|
Low | 35 | W | OSPAR 2008 | BAC limit |
Atlantic cod, muscle
|
Gadus Morhua
|
High | 500 | W | EU 2006 |
Foodstuffs limit for "meat of fish molluscs", Regulation (EC) No. 1881/2006
|
Herring, muscle
|
Clupea harengus
|
Low | 35 | W | OSPAR 2008 | BAC limit |
Herring, muscle
|
Clupea harengus
|
High | 500 | W | EU 2006 |
Foodstuffs limit for "meat of fish molluscs", Regulation (EC) No. 1881/2006
|
LEAD | ||||||
Mussels |
Mytilus¹sp.
|
Low | 1300 | D | OSPAR 2008 | BAC limit |
Mussels |
Mytilus sp.
|
High | 7500 | D | EU 2006 |
Foodstuffs limit for "bivalve molluscs", Regulation (EC) No. 1881/2006, conversion assuming 20% wet weight (cf. OSPAR CEMP assessment manual 2008, Table 2.1)
|
Atlantic cod, liver |
Gadus morhua
|
Low | 26 | W | OSPAR 2008 | BAC limit |
Atlantic cod, liver |
Gadus morhua
|
High | 1500 | W | EU 2006 |
Foodstuffs limit for "bivalve molluscs", Regulation (EC) No. 1881/2006
|
Herring, muscle |
Clupea harengus
|
Low | 26 | W | OSPAR 2008 | BAC limit |
Herring, muscle |
Clupea harengus
|
High | 1500 | W | EU 2006 |
Foodstuffs limit for "bivalve molluscs", Regulation (EC) No. 1881/2006
|
HCB | ||||||
Mussels |
Mytilus¹sp.
|
Low | 0, 63 | D | OSPAR 2008 | BAC limit |
Mussels |
Mytilus sp.
|
High | 6,3 | D | Taken as 10 times "Low" (or approximately the median of High: Low ratio for CBs in mussel, which is 8.6) | |
Atlantic cod, liver |
Gadus morhua
|
Low | 0,18 | L | OSPAR 2008 | BAC limit times 2 (OSPAR²) |
Atlantic cod, liver |
Gadus morhua
|
High | 135 | L | Taken as 750 times "Low" (median of High: Low ratio for CBs in cod) | |
Herring, muscle |
Clupea harengus
|
Low | 1,8 | L | OSPAR 2008 | BAC² limit times 20 (OSPAR²) |
Herring, muscle |
Clupea harengus
|
High | 135 | L | Taken as the same for cod, in pattern with CBs EAC´s | |
LINDANE | ||||||
Mussels |
Mytilus¹sp.
|
Low | 0,97 | D | OSPAR 2008 | BAC limit |
Mussels |
Mytilus sp.
|
High | 1,45 | D | OSPAR 2008 | EAC limit |
Atlantic cod, liver |
Gadus morhua
|
Low | 0,29 | L | Taken as 1/750times "High" (median of Low:High ratio for CBs in cod) | |
Atlantic cod, liver |
Gadus morhua
|
High | 220 | L | Taken as the same as for herring | |
Herring, muscle |
Clupea harengus
|
Low | 2,9 | L | Taken as 10 times value for cod, as | |
Herring, muscle |
Clupea harengus
|
High | 220 | L | OSPAR 2008 | Taken as OSPAR EAC (2008) = 11 times 20 (to convert wet weight to lipid weight - (OSPAR²) = 220 ppb l.w. |
PCB (CB28) | ||||||
Mussels |
Mytilus¹sp.
|
Low | 0,75 | D | OSPAR 2008 | BAC limit |
Mussels |
Mytilus sp.
|
High | 3,2 | D | OSPAR 2008 | EAC limit |
Atlantic cod, liver |
Gadus morhua
|
Low | 0,2 | W | OSPAR 2008 | BAC limit times 2 (OSPAR²) |
Atlantic cod, liver |
Gadus morhua
|
High | 64 | L | OSPAR 2008 | EAC limit |
Herring, muscle |
Clupea harengus
|
Low | 2 | W | OSPAR 2008 | BAC limit times 20 (OSPAR²) |
Herring, muscle |
Clupea harengus
|
High | 64 | L | OSPAR 2008 | EAC limit |
PCB (CB 52) | ||||||
Mussels |
Mytilus¹sp.
|
Low | 0,75 | D | OSPAR 2008 | BAC limit |
Mussels |
Mytilus sp.
|
High | 5,4 | D | OSPAR 2008 | EAC limit |
Atlantic cod, liver |
Gadus morhua
|
Low | 0,16 | W | OSPAR 2008 | BAC limit times 2 (OSPAR²) |
Atlantic cod, liver |
Gadus morhua
|
High | 108 | L | OSPAR 2008 | EAC limit |
Herring, muscle |
Clupea harengus
|
Low | 1,6 | W | OSPAR 2008 | BAC limit times 20 (OSPAR²) |
Herring, muscle |
Clupea harengus
|
High | 108 | L | OSPAR 2008 | EAC limit |
PCB (CB 101) | ||||||
Mussels |
Mytilus¹sp.
|
Low | 0,7 | D | OSPAR 2008 | BAC limit |
Mussels |
Mytilus sp.
|
High | 6 | D | OSPAR 2008 | EAC limit |
Atlantic cod, liver | Gadus morhua | Low | 0,16 | W | OSPAR 2008 |
BAC limit times 2 (OSPAR²)
|
Atlantic cod, liver | Gadus morhua | High | 120 | L | OSPAR 2008 | EAC limit |
Herring, muscle | Clupea harengus | Low | 1,6 | W | OSPAR 2008 |
BAC limit times 20 (OSPAR²)
|
Herring, muscle |
Clupea harengus
|
High | 120 | L | OSPAR 2008 | EAC limit |
PCB (CB 118) | ||||||
Mussels |
Mytilus¹sp.
|
Low | 0,6 | D | OSPAR 2008 | BAC limit |
Mussels | Mytilus sp. | High | 1,2 | D | OSPAR 2008 | EAC limit |
Atlantic cod, liver | Gadus morhua | Low | 0,2 | W | OSPAR 2008 |
BAC limit times 2 (OSPAR²)
|
Atlantic cod, liver | Gadus morhua | High | 24 | L | OSPAR 2008 | EAC limit |
Herring, muscle | Clupea harengus | Low | 2 | W | OSPAR 2008 |
BAC limit times 20 (OSPAR²)
|
Herring, muscle | Clupea harengus | High | 24 | L | OSPAR 2008 | EAC limit |
PCB (CB 138) | ||||||
Mussels |
Mytilus¹sp.
|
Low | 0,6 | D | OSPAR 2008 | BAC limit |
Mussels | Mytilus sp. | High | 15,8 | D | OSPAR 2008 | EAC limit |
Atlantic cod, liver | Gadus morhua | Low | 0,18 | W | OSPAR 2008 |
BAC limit times 2 (OSPAR²)
|
Atlantic cod, liver | Gadus morhua | High | 316 | L | OSPAR 2008 | EAC limit |
Herring, muscle | Clupea harengus | Low | 1,8 | W | OSPAR 2008 |
BAC limit times 20 (OSPAR²)
|
Herring, muscle | Clupea harengus | High | 316 | L | OSPAR 2008 | EAC limit |
PCB (CB 153) | ||||||
Mussels |
Mytilus¹sp.
|
Low | 0,6 | D | OSPAR 2008 | BAC limit |
Mussels |
Mytilus sp.
|
High | 80 | D | OSPAR 2008 | EAC limit |
Atlantic cod, liver | Gadus morhua | Low | 0,2 | W | OSPAR 2008 |
BAC limit times 2 (OSPAR²)
|
Atlantic cod, liver | Gadus morhua | High | 1600 | L | OSPAR 2008 | EAC limit |
Herring, muscle | Clupea harengus | Low | 2 | W | OSPAR 2008 |
BAC limit times 20 (OSPAR²) |
Herring, muscle | Clupea harengus | High | 1600 | L | OSPAR 2008 | EAC limit |
PCB (CB 180) | ||||||
Mussels |
Mytilus¹sp. |
Low | 0,6 | D | OSPAR 2008 | BAC limit |
Mussels | Mytilus sp. | High | 24 | D | OSPAR 2008 | EAC limit |
Atlantic cod, liver | Gadus morhua | Low | 0,22 | W | OSPAR 2008 |
BAC limit times 2 (OSPAR²) |
Atlantic cod, liver | Gadus morhua | High | 480 | L | OSPAR 2008 |
EAC limit |
Herring, muscle | Clupea harengus | Low | 2,2 | W | OSPAR 2008 |
BAC limit times 20 (OSPAR²) |
Herring, muscle | Clupea harengus | High | 480 | L | OSPAR 2008 | EAC limit |
DDE,p,p’ (as DDT representative) |
||||||
Mussels |
Mytilus¹sp. |
Low | 0,63 | D | OSPAR 2008 | BAC limit |
Mussels | Mytilus sp. | High | 6,3 | D | Taken as 10 minutes "Low" | |
Atlantic cod, liver | Gadus morhua | Low | 0,2 | L | OSPAR 2008 | BAC limit takes |
Atlantic cod, liver | Gadus morhua | High | 150 | L | Taken as 750 times "Low" (median of High: Low ratio for CBs) | |
Herring, muscle | Clupea harengus | Low | 2 | L | OSPAR 2008 | BAC limit times 20 (OSPAR) |
Herring, muscle | Clupea harngus | High | 150 | Taken as the same for cod, in pattern with CB´s EA |
¹) Blue mussel (Mytilus edulis) for the north-east Atlantic, Mediterranean mussel (M. galloprovincialis) for the Mediterranean and Black Sea.
²) Used in the OSPAR statistical assessment (R.Fryer (Marine Lab., UK) pers. comm.)
Table 2: Limit concentration used for classification in figures and maps in 2014 assessment:
Low/High concentration limits for spatial assessment, which delimits the classes Low, Moderate (Low < Assessment level < High) and High. EU foodstuff limits are derived from Regulation (EC) No. 1861/2006. Except for EU legislation, the limits have no legal application. All values are expressed in units of µg/kg and on a wet weight (W) except for organics in herring which is expressed on a fat weight (L) basis. Unless otherwise noted, all values are derived from OSPAR Background Assessment Concentration (BAC) or Environmental Assessment Criteria (EAC) or use of the foodstuff limits are as applied in the OSPAR assessment 2013; the exceptions being the High values for DDE and HCB and the Low values for Lindane (g-HCH).
Species Code |
Substance |
Tissue |
Basis |
Low |
High |
Comment |
Clupea harengus |
PCB congener CB101 |
muscle |
L |
1,78 |
121,0 |
Low converted to lw assuming 4.5% lipid content |
Clupea harengus |
PCB congener CB118 |
muscle |
L |
2,22 |
25,0 |
Low converted to lw assuming 4.5% lipid content |
Clupea harengus |
PCB congener CB138 |
muscle |
L |
2,00 |
317,0 |
Low converted to lw assuming 4.5% lipid content |
Clupea harengus |
PCB congener CB153 |
muscle |
L |
2,22 |
1 585,0 |
Low converted to lw assuming 4.5% lipid content |
Clupea harengus |
PCB congener CB180 |
muscle |
L |
2,44 |
469,0 |
Low converted to lw assuming 4.5% lipid content |
Clupea harengus |
PCB congener CB28 |
muscle |
L |
2,22 |
67,0 |
Low converted to lw assuming 4.5% lipid content |
Clupea harengus |
PCB congener CB52 |
muscle |
L |
1,78 |
108,0 |
Low converted to lw assuming 4.5% lipid content |
Clupea harengus |
Cadmium - Cd |
liver |
W |
26,00 |
1 000,0 |
High taken as EC for bivalve tissue |
Clupea harengus |
DDT metabolite DDE |
muscle |
L |
2,22 |
151,3 |
High taken as median of High:Low CB-ratios times Low |
Clupea harengus |
Hexachlorobenzene - HCB |
muscle |
L |
2,00 |
136,1 |
High taken as median of High:Low CB-ratios times Low |
Clupea harengus |
Hexachlorocyclohexane- a-HCH, Lindane |
muscle |
L |
3,59 |
244,4 |
Low taken as median of High:Low CB-ratios divided by High |
Clupea harengus |
Mercury - Hg |
muscle |
W |
35,00 |
500,0 |
High from foodstuffs limit for "muscle meat of fish" |
Clupea harengus |
Lead - Pb |
liver |
W |
26,00 |
1 500,0 |
High taken as EC for bivalve tissue |
Gadus morhua |
PCB congener CB101 |
liver |
W |
0,08 |
54,5 |
Converted to ww assuming 45% lipid content |
Gadus morhua |
PCB congener CB118 |
liver |
W |
0,10 |
11,3 |
Converted to ww assuming 45% lipid content |
Gadus morhua |
PCB congener CB138 |
liver |
W |
0,09 |
142,7 |
Converted to ww assuming 45% lipid content |
Gadus morhua |
PCB congener CB153 |
liver |
W |
0,10 |
713,3 |
Converted to ww assuming 45% lipid content |
Gadus morhua |
PCB congener CB180 |
liver |
W |
0,11 |
211,1 |
Converted to ww assuming 45% lipid content |
Gadus morhua |
PCB congener CB28 |
liver |
W |
0,10 |
30,2 |
Converted to ww assuming 45% lipid content |
Gadus morhua |
PCB congener CB52 |
liver |
W |
0,08 |
48,6 |
Converted to ww assuming 45% lipid content |
Gadus morhua |
Cadmium - Cd |
liver |
W |
26,00 |
1 000,0 |
High taken as EC for bivalve tissue |
Gadus morhua |
DDT metabolite DDE |
liver |
W |
0,10 |
68,1 |
High taken as median of High:Low CB-ratios times Low |
Gadus morhua |
Hexachlorobenzene – HCB |
liver |
W |
0,09 |
61,3 |
High taken as median of High:Low CB-ratios times Low |
Gadus morhua |
Hexachlorocyclohexane - a-HCH, Lindane |
liver |
W |
0,02 |
11,0 |
Low taken as median of High:Low CB-ratios divided by High |
Gadus morhua |
Mercury - Hg |
muscle |
W |
35,00 |
500,0 |
High from foodstuffs limit for "muscle meat of fish" |
Gadus morhua |
Lead - Pb |
liver |
W |
26,00 |
1 500,0 |
High taken as EC for bivalve tissue |
Mytilus edulis |
Benzo[a]pyrene - BaP |
soft body |
W |
0,24 |
102,0 |
Converted to ww assuming 17% |
Mytilus edulis |
PCB congener CB101 |
soft body |
W |
0,12 |
1,0 |
Converted to ww assuming 17% for BAC and 1.3% lipid content |
Mytilus edulis |
PCB congener CB118 |
soft body |
W |
0,10 |
0,2 |
Converted to ww assuming 17% for BAC and 1.3% lipid content |
Mytilus edulis |
PCB congener CB138 |
soft body |
W |
0,10 |
2.7 |
Converted to ww assuming 17% for BAC and 1.3% lipid content |
Mytilus edulis |
PCB congener CB153 |
soft body |
W |
0,10 |
13.6 |
Converted to ww assuming 17% for BAC and 1.3% lipid content |
Mytilus edulis |
PCB congener CB180 |
soft body |
W |
0,10 |
4.1 |
Converted to ww assuming 17% for BAC and 1.3% lipid content |
Mytilus edulis |
PCB congener CB28 |
soft body |
W |
0,13 |
0,5 |
Converted to ww assuming 17% for BAC and 1.3% lipid content |
Mytilus edulis |
PCB congener CB52 |
soft body |
W |
0,13 |
0.9 |
Converted to ww assuming 17% for BAC and 1.3% lipid content |
Mytilus edulis |
Cadmium - Cd |
soft body |
W |
163,20 |
1 000,0 |
Low converted to ww assuming 17%. High from foodstuffs limit for "bivalve molluscs" |
Mytilus edulis |
DDT metabolite DDE |
soft body |
W |
0,11 |
1,4 |
High taken as median of High:Low CB-ratios times Low |
Mytilus edulis |
Hexachlorobenzene – HCB |
soft body |
W |
0,11 |
1,4 |
High taken as median of High:Low CB-ratios times Low |
Mytilus edulis |
Hexachlorocyclohexane - a-HCH, Lindane |
soft body |
W |
0,16 |
0,2 |
Converted to ww assuming 17% |
Mytilus edulis |
Mercury - Hg |
soft body |
W |
15,30 |
500,0 |
Low converted to ww assuming 17%. High from foodstuffs limit for "fisheries products" |
Mytilus edulis |
Lead - Pb |
soft body |
W |
221,00 |
1 500,0 |
Low converted to ww assuming 17%. High from foodstuffs limit for "bivalve molluscs" |
Mytilus galloprovincialis |
Benzo[a]pyrene - BaP |
soft body |
W |
0,27 |
114,0 |
Converted to ww assuming 19% |
Mytilus galloprovincialis |
PCB congener CB101 |
soft body |
W |
0,13 |
1.1 |
Converted to ww assuming 19% for BAC and 2.0% lipid content |
Mytilus galloprovincialis |
PCB congener CB118 |
soft body |
W |
0,11 |
0,2 |
Converted to ww assuming 19% for BAC and 2.0% lipid content |
Mytilus galloprovincialis |
PCB congener CB138 |
soft body |
W |
0,11 |
3.0 |
Converted to ww assuming 19% for BAC and 2.0% lipid content |
Mytilus galloprovincialis |
PCB congener CB153 |
soft body |
W |
0,11 |
15.2 |
Converted to ww assuming 19% for BAC and 2.0% lipid content |
Mytilus galloprovincialis |
PCB congener CB180 |
soft body |
W |
0,11 |
4.6 |
Converted to ww assuming 19% for BAC and 2.0% lipid content |
Mytilus galloprovincialis |
PCB congener CB28 |
soft body |
W |
0,14 |
0.6 |
Converted to ww assuming 19% for BAC and 2.0% lipid content |
Mytilus galloprovincialis |
PCB congener CB52 |
soft body |
W |
0,14 |
1.0 |
Converted to ww assuming 19% for BAC and 2.0% lipid content |
Mytilus galloprovincialis |
Cadmium - Cd |
soft body |
W |
182,40 |
1 000,0 |
Low converted to ww assuming 19%. High from foodstuffs limit for "bivalve molluscs" |
Mytilus galloprovincialis |
DDT metabolite DDE |
soft body |
W |
0,12 |
2,2 |
High taken as median of High:Low CB-ratios times Low |
Mytilus galloprovincialis |
Hexachlorobenzene – HCB |
soft body |
W |
0,12 |
2,2 |
High taken as median of High:Low CB-ratios times Low |
Mytilus galloprovincialis |
Hexachlorocyclohexane - a-HCH, Lindane |
soft body |
W |
0,18 |
0,3 |
Converted to ww assuming 19% |
Mytilus galloprovincialis |
Mercury - Hg |
soft body |
W |
17,10 |
500,0 |
Low converted to ww assuming 19%. High from foodstuffs limit for "fisheries products" |
Mytilus galloprovincialis |
Lead - Pb |
soft body |
W |
247,00 |
1 500,0 |
Low converted to ww assuming 19%. High from foodstuffs limit for "bivalve molluscs" |
Platichthys flesus |
PCB congener CB101 |
liver |
W |
0,08 |
15,7 |
Converted to ww assuming 13% lipid content |
Platichthys flesus |
PCB congener CB118 |
liver |
W |
0,10 |
3,3 |
Converted to ww assuming 13% lipid content |
Platichthys flesus |
PCB congener CB138 |
liver |
W |
0,09 |
41,2 |
Converted to ww assuming 13% lipid content |
Platichthys flesus |
PCB congener CB153 |
liver |
W |
0,10 |
206,1 |
Converted to ww assuming 13% lipid content |
Platichthys flesus |
PCB congener CB180 |
liver |
W |
0,11 |
61,0 |
Converted to ww assuming 13% lipid content |
Platichthys flesus |
PCB congener CB28 |
liver |
W |
0,10 |
8,7 |
Converted to ww assuming 13% lipid content |
Platichthys flesus |
PCB congener CB52 |
liver |
W |
0,08 |
14,0 |
Converted to ww assuming 13% lipid content |
Platichthys flesus |
Cadmium - Cd |
muscle |
W |
26,00 |
1 000,0 |
High taken as EC for bivalve tissue |
Platichthys flesus |
DDT metabolite DDE |
liver |
W |
0,10 |
19,7 |
High taken as median of High:Low CB-ratios times Low |
Platichthys flesus |
Hexachlorobenzene – HCB |
liver |
W |
0,09 |
17,7 |
High taken as median of High:Low CB-ratios times Low |
Platichthys flesus |
Hexachlorocyclohexane - a-HCH, Lindane |
liver |
W |
0,06 |
11,0 |
Low taken as median of High:Low CB-ratios divided by High |
Platichthys flesus |
Mercury - Hg |
muscle |
W |
35,00 |
500,0 |
High from foodstuffs limit for "muscle meat of fish" |
Platichthys flesus |
Lead - Pb |
muscle |
W |
26,00 |
1 500,0 |
High taken as EC for bivalve tissue |
Pleuronectes platessa |
PCB congener CB101 |
liver |
W |
0,08 |
12,1 |
Converted to ww assuming 10% lipid content |
Pleuronectes platessa |
PCB congener CB118 |
liver |
W |
0,10 |
2,5 |
Converted to ww assuming 10% lipid content |
Pleuronectes platessa |
PCB congener CB138 |
liver |
W |
0,09 |
31,7 |
Converted to ww assuming 10% lipid content |
Pleuronectes platessa |
PCB congener CB153 |
liver |
W |
0,10 |
158,5 |
Converted to ww assuming 10% lipid content |
Pleuronectes platessa |
PCB congener CB180 |
liver |
W |
0,11 |
46,9 |
Converted to ww assuming 10% lipid content |
Pleuronectes platessa |
PCB congener CB28 |
liver |
W |
0,10 |
6,7 |
Converted to ww assuming 10% lipid content |
Pleuronectes platessa |
PCB congener CB52 |
liver |
W |
0,08 |
10,8 |
Converted to ww assuming 10% lipid content |
Pleuronectes platessa |
Cadmium - Cd |
muscle |
W |
26,00 |
1 000,0 |
High taken as EC for bivalve tissue |
Pleuronectes platessa |
DDT metabolite DDE |
liver |
W |
0,10 |
15,1 |
High taken as median of High:Low CB-ratios times Low |
Pleuronectes platessa |
Hexachlorobenzene – HCB |
liver |
W |
0,09 |
13,6 |
High taken as median of High:Low CB-ratios times Low |
Pleuronectes platessa |
Hexachlorocyclohexane - a-HCH, Lindane |
liver |
W |
0,07 |
11,0 |
Low taken as median of High:Low CB-ratios divided by High |
Pleuronectes platessa |
Mercury - Hg |
muscle |
W |
35,00 |
500,0 |
High from foodstuffs limit for "muscle meat of fish" |
Pleuronectes platessa |
Lead - Pb |
muscle |
W |
26,00 |
1 500,0 |
High taken as EC for bivalve tissue |
1) Concerns blue mussel (Mytilus edulis) for the North-East Atlantic, Mediterranean mussel (M. galloprovincialis) for the Mediterranean Sea and Black Sea.
2) Used in the OSPAR statistical assessment (R.Fryer (Marine Lab., UK) pers. comm.)
The assessment method does not require that time series be complete, so no measures are being taken to fill such gaps. Instead, the method adapts to the existing gaps in the time series.
The regional assessments are based on tallies of results for single time series within each region, without further consideration of geographical distribution within the region. Gaps in the geographical coverage will mean that the regional assessment may not be representative for the region as a whole. There is no attempt to extrapolate results from existing data to estimate conditions in geographical areas without data.
Aggregated data does not necessarily convey the uncertainty these problems cause. Also, the time coverage is very variable between series and some of the trends shown may be based on mainly older data. The statistical significance of trends is based on a two-sided test with a nominal 5% significance level, separately for each time series, without regard to serial correlation. Assessments of 'No trend' (i.e. no statistically significant trend) may be due both to actual lack of trend and to insufficient data (too few years in the data series; values in general below reporting limit, giving many ties).
This assessment is based on data reported to the EEA by EEA member countries, which have significant gaps in terms of availability (geographical and temporal) and consistency, especially for the Mediterranean and Black Seas. These data uncertainties, therefore, hinder more adequate assessment of concentrations and trends of hazardous substances in European marine waters.
The classification of levels reflects both observed levels and the uncertainty in trends or levels indicated by data. Thus a Red classification does not necessarily mean that estimated levels are above the limit; it may merely indicate that the uncertainty is so large (because of little data and/or high variability) that it cannot be assessed with reasonable confidence that the true level is below the highest limit. It should also be noted that the three-class system applied for concentrations of hazardous substances in fish does not highlight those cases where there is a risk to human consumption.
More generally, it should also be noted that considerable efforts have been made (i.e. policy, management and research levels) to establish and maintain monitoring programmes to assess the level, trends and effects of hazardous substances in biota, and to select the preferred indicator tissues in particular species. However, there is a lack of reliable and consistent data for many hazardous substances and for several regions. Although basic legislation is in place to combat excessive exposure, specific assessment criteria with respect to levels, trends and effects need to be further developed for the indicator matrices. Furthermore, measurement of concentrations in biota are not coordinated with measurements of inputs, which enhances the uncertainty in the correlation between the two.
It should also be noted that this indicator should not be used as an assessment of compliance monitoring in relation to the Water Framework Directive, mainly because the monitoring strategy and assessment criteria are for the status of hazardous substances in biota, whereas the Water Framework Directive EQS concerns concentrations in water for the most part. The exceptions include mercury and HCB in “prey tissue”, i.e. the whole individual, which would only apply to mussels in this indicator. There is a provision under EQSD that allows Member States to establish other EQS in biota (and sediment) for other substances as long as they would provide the same level of protection. The ongoing development of technical guidance for deriving environmental quality standards for the Water Framework Directive should help Member States if they choose this solution. In addition to this, these indicators will also have to take account of new legislation, for example technical specifications for chemical analysis (2009/90/EC).
For references, please go to https://www.eea.europa.eu/data-and-maps/indicators/hazardous-substances-in-marine-organisms/hazardous-substances-in-marine-organisms-1 or scan the QR code.
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