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Report 601779002/2009 E.A.J. Bleeker | E.M.J. Verbruggen Bioaccumulation of polycyclic aromatic hydrocarbons in aquatic organisms
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Page 1: RIVM report 601779002 Bioaccumulation of polycyclic ... · The present report gives an evaluation of reported BCF values for polycyclic aromatic hydrocarbons (PAHs) in aquatic organisms.

Report 601779002/2009

E.A.J. Bleeker | E.M.J. Verbruggen

Bioaccumulation of polycyclic aromatichydrocarbons in aquatic organisms

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RIVM report 601779002/2009

Bioaccumulation of polycyclic aromatic hydrocarbons in aquatic organisms

E.A.J. Bleeker E.M.J. Verbruggen Contact: E.A.J. Bleeker Expertise Centre for Substances [email protected]

This investigation has been performed by order and for the account of the Ministry of Housing, Spatial Planning and the Environment (VROM), within the framework of the project ‘Strategic research for REACH’ (M/601779)

RIVM, P.O. Box 1, 3720 BA Bilthoven, the Netherlands Tel +31 30 274 91 11 www.rivm.nl

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© RIVM 2009 Parts of this publication may be reproduced, provided acknowledgement is given to the 'National Institute for Public Health and the Environment', along with the title and year of publication.

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Abstract Bioaccumulation of polycyclic aromatic hydrocarbons in aquatic organisms RIVM has evaluated the available data on bioaccumulation of polycyclic aromatic hydrocarbons (PAHs) in aquatic organisms. As a result the categorisation of PAHs regarding their bioaccumulation potential was adapted. Phenanthrene and fluoranthene are now no longer considered ‘very bioaccumulative’ in fish, but ‘bioaccumulative’.

The level of accumulation of compounds in organisms (bioaccumulation) is an important criterion in chemicals regulation. It gives an indication that higher in the food chain higher concentrations of a compound are found that may become harmful. Data on individual PAHs, including data on bioaccumulation, are used in risk assessment of (mixtures of) compounds in which PAHs are major components, e.g. oil and oil compounds.

As measure for accumulation the bioconcentration factor (BCF) of a compound is used. This is defined as the ratio between the uptake rate of a compound from water into the organism and its elimination rate to water. In the European REACH legislation compounds are divided over three BCF categories: not bioaccumulative (BCF is below 2000), bioaccumulative (BCF is between 2000 and 5000) and very bioaccumulative (BCF is above 5000).

Fish are capable of transforming PAHs into compounds that are better soluble in water, which facilitates elimination. This results in lower measured BCF values in fish. Mussels and other invertebrates are much less capable of PAH transformation, which results in higher accumulation of PAHs in these organisms. Key words: bioaccumulation, polycyclic aromatic hydrocarbons (PAHs), risk assessment

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Rapport in het kort Bioaccumulatie van polycyclische aromatische koolwaterstoffen in waterorganismen Het RIVM heeft beschikbare gegevens over ophopingen van polycyclische aromatische koolwaterstoffen (PAK’s) in waterorganismen geëvalueerd. Naar aanleiding hiervan is de indeling van deze stoffen voor regelgeving aangepast. Fenantreen en fluoranteen worden nu niet meer als ‘zeer bioaccumulerend’ beschouwd in vis, maar als ‘bioaccumulerend’.

De mate waarin stoffen in organismen ophopen (bioaccumulatie) is een belangrijk criterium voor regelgeving. Het is een indicatie dat hoger in de voedselketen hogere concentraties van de stof worden aangetroffen die schadelijk kunnen zijn. Gegevens van individuele PAK’s, waaronder bioaccumulatie-gegevens, worden gebruikt voor de risicobeoordeling van stoffen(mengsels) waarin PAK’s een belangrijk bestanddeel zijn, zoals bijvoorbeeld olie en olieachtige stoffen.

Als maat voor de ophoping wordt de bioconcentratiefactor (BCF) van een stof gebruikt. Dat is de ratio tussen de snelheid waarmee het organisme de stof vanuit water opneemt en de snelheid waarmee het naar water wordt uitgescheiden. Op grond hiervan worden stoffen in de Europese REACH-regelgeving ingedeeld in drie categorieën: niet bioaccumulerend (de BCF is kleiner dan 2000), bioaccumulerend (de BCF ligt tussen 2000 en 5000) en zeer bioaccumulerend (de BCF is hoger dan 5000).

Vissen zijn in staat om PAK’s om te zetten in stoffen die beter in water oplosbaar zijn waardoor ze makkelijker kunnen worden uitgescheiden. Hierdoor worden in vissen vaak lagere BCF-waarden gemeten. Mosselen en andere ongewervelden kunnen PAK’s veel minder goed omzetten waardoor PAK’s in deze organismen meer ophopen. Trefwoorden: bioaccumulatie, polycyclische aromatische koolwaterstoffen (PAK’s), risicobeoordeling

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Contents

Summary 7

1 Introduction 9

2 Methods 11

3 Results 13 3.1 Reliability of reported BCF values 13 3.2 Additional data 13 3.3 Evaluation of reliable BCF values 15 4 Discussion 21 4.1 Evaluating the bioaccumulation assessment by Lampi and Parkerton 21 4.2 Evaluating the bioaccumulation assessment in the RAR 23 4.3 Dietary bioaccumulation studies 24 4.4 Using bioaccumulation data for regulatory purposes 25 References 29

Annex I Overview of BCF values from studies that were rated as not reliable (validity 3) 37

Annex II Overview of BCF values from studies for which validity was not assignable (validity 4) 47

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Summary In risk assessment the potential of a substance to accumulate in a food web is an important criterion. Bioaccumulation may result in increasing internal concentrations in organisms higher in the food chain and then it is called biomagnification. Whether this process of biomagnification actually takes place depends on the properties of the compound itself (e.g. stability, lipophilicity) and on the organisms in the food chain (ability to metabolize and/or excrete the compound). This may result in situations where at lower trophic levels bioaccumulation and biomagnification take place, while higher in the food chain organisms are capable of handling the compound and efficiently excreting it. In the present report and in agreement with regulatory frameworks, therefore, bioaccumulation data on fish (higher in the food chain) and other aquatic organisms (lower in the food chain) are evaluated. These organisms include, but are not restricted to molluscs, crustaceans, insects, oligochaetes and polychaetes.

As a measure for bioaccumulation usually the bioconcentration factor (BCF) is used as a trigger. The BCF is defined as the ratio between uptake and depuration rates, which in a steady state situation equals the ratio between the internal concentration in an organism and the concentration in water. Since this ratio not only depends on compound properties and test organisms, but also on the test setup used, quality criteria for testing and reporting bioconcentration have been debated. Using such criteria in the present report reliabilities of reported BCF values for polycyclic aromatic hydrocarbons (PAHs) in aquatic organisms are evaluated, focussing on the 16 PAHs defined as priority substances by the United States Environmental Protection Agency (naphthalene, acenaphthene, acenaphthylene, 9H-fluorene, anthracene, phenanthrene, fluoranthene, pyrene, benz[a]anthracene, chrysene, benzo[a]pyrene, benzo[b]fluoranthene, benzo[k]fluoranthene, benzo[ghi]perylene, dibenz[a,h]anthracene, and indeno-[1,2,3-cd]pyrene).

Based on existing databases and reviews, as well as a search in the recent literature, 133 original papers were examined to evaluate the reliability of 855 BCF values.

Only about 34% of these values were deemed reliable (in many cases with restrictions), but another 40% were deemed not assignable (due to lack of information in the report).

As part of the present study the (re-)evaluated BCFs are compared with previous evaluations of BCF studies and differences in opinion are discussed. Also the role of dietary uptake is discussed but it is concluded that at present not enough data are available to use and compare bioaccumulation data from dietary studies with those from aqueous tests.

Finally the evaluation is summarized and conclusions on bioaccumulation potential for each of the 16 PAHs are given, applying the triggers as used in the EU-legislation REACH: compounds are considered as bioaccumulative (B) when their BCF is between 2000 and 5000 and very bioaccumulative (vB) when the BCF is >5000. Naphthalene, acenaphthene, acenaphthylene and 9H-fluorene are considered not bioaccumulative. Anthracene, phenanthrene and fluoranthene are considered B for fish, but they are vB at lower trophic levels (molluscs, crustaceans). Pyrene, benz[a]anthracene and benzo[a]pyrene do not accumulate in fish (due to biotransformation), but are vB at lower trophic levels. For chrysene, benzo[k]fluoranthene, benzo[ghi]perylene, and dibenz[a,h]anthracene only reliable data on daphnids are available which deem these compounds as vB. For benzo[b]fluoranthene and indeno[1,2,3-cd]pyrene no reliable data are available at all, so bioaccumulative potential could not be established.

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1 Introduction In risk assessment the degree of bioaccumulation of a compound is an important criterion. This is based on the assumption that compounds that accumulate in organisms can accumulate in a food web, resulting in higher internal concentrations in organisms higher in the food chain. This process is known as biomagnification. Whether biomagnification will actually take place depends on the physicochemical properties of the compound (e.g. stability, lipophilicity) and on the organism(s) that take up the compound (ability to metabolize and/or excrete the compound) (Gobas et al., 2009). This may result in situations where at lower trophic levels bioaccumulation and biomagnification takes place, while higher in the food chain organisms are capable of handling the compound and efficiently excreting it (e.g. Wang and Wang, 2006; Wan et al., 2007; Nfon et al., 2008; Takeuchi et al., 2009). Nevertheless, specifically this metabolization may activate the toxicity of some compounds. For regulatory purposes the process of biomagnification is often simplified by assessing the bioaccumulation, especially in fish. According to the European REACH1 legislation, however, ‘the assessment of bioaccumulation shall be based on measured data on bioconcentration in aquatic species’ (EU, 2007). Also in other frameworks (e.g. Stockholm Convention, 2001) assessment of bioaccumulation is not restricted to fish, so in this report bioaccumulation data on other aquatic organisms are evaluated as well.

In aquatic tests the degree of bioaccumulation is usually expressed as a bioconcentration factor (BCF), defined as the ratio between uptake from water into an organism and elimination from an organism to water. In a steady state situation this ratio is independent of time and then it equals the ratio between the concentration in the organism and the concentration in water.

The BCF is used as a trigger for bioaccumulation in several regulatory frameworks (e.g. REACH, OSPAR2, GHS3), but the trigger values in these frameworks may differ. In this report we focus on the triggers defined in REACH: a compound is defined as bioaccumulative (B) when the wet-weight BCF value (normalized to lipid content) is higher than 2000 and as very bioaccumulative (vB) if this value is higher than 5000. Lipid normalization is applied when bioaccumulating compounds tend to accumulate in the lipids of organisms (ECHA, 2008), resulting in higher BCF values for organisms with higher lipid content. To enable comparison between species BCF values are normalized to an organism that contains 5% lipids, the average value for the small fish species used in OECD guideline 305 (OECD, 1996; Tolls et al., 2000).

The degree of bioaccumulation of compounds depends on several factors. First of all, it depends on the compound tested and its properties as well as the test species used, but in addition several test conditions have an influence, e.g. the time of exposure, the type of exposure (static vs. continuous flow), etc. To minimize variation between tests guidelines were developed in which test conditions were described (e.g. OECD, 1996). Still comparisons between bioaccumulation studies are difficult, because quite a few data were generated before guidelines were established. In addition, in some cases not all relevant details on the test setup are described. This has lead to a debate to come to quality criteria for BCF values (e.g. Parkerton et al., 2008), as this is seen as essential in getting a clearer picture on the possibility of predicting BCF values from physicochemical properties of compounds.

The present report gives an evaluation of reported BCF values for polycyclic aromatic hydrocarbons (PAHs) in aquatic organisms. By examining the studies in detail the reliability of reported values is

1 REACH: Registration, Evaluation, Authorisation and restriction of CHemicals. 2 OSPAR: OSlo and PARis conventions (OSPAR, 1992). 3 GHS: Global Harmonizing System of classification and labelling of chemicals.

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examined. The study was limited to the 16 PAHs defined as priority substances by the United States Environmental Protection Agency (US EPA; http://www.epa.gov/waterscience/methods/pollutants.htm; further indicated as EPA-PAHs, Figure 1

indeno[1,2,3-cd]pyrene

benzo[ghi]perylene

benzo[a]pyrene

pyrene

anthracene

acenaphthene

benzo[k]fluoranthene

chrysene

fluoranthene

9H-fluorene

naphthalene

dibenz[a,h]anthracene

benzo[b]fluoranthene

benz[a]anthracene

phenanthrene

acenaphthylene

Figure 1: Structural formulae of the 16 polycyclic aromatic hydrocarbons defined as priority substances by the United States Environmental Protection Agency.

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2 Methods In collecting reported BCF values the following sources were used to create an overview.

− The Ecotoxicology Database (ECOTOX) of the US EPA. This database is a source for locating single chemical toxicity data for aquatic life, terrestrial plants and wildlife. ECOTOX was created and is maintained by the US EPA, Office of Research and Development (ORD), and the National Health and Environmental Effects Research Laboratory’s (NHEERL’s) Mid-Continent Ecology Division (MED). It is publicly available at the internet (http://cfpub.epa.gov/ecotox/).

− The bioconcentration Gold Standard Database of the European Academy of Standardization (EURAS). This database was established in 2006 in the framework of the Cefic Long-range Research Initiative. Cefic is de European Chemical Industry Council, representing the European chemical industry. The database is linked to the AMBIT database and available at http://ambit.acad.bg.

− The database of the Japanese National Institute of Technology and Evaluation. The Chemical Management Field of this institute aims at collecting and transmitting information required for total risk assessment and management of chemical substances. Their Biodegradation and Bioconcentration database is available in English at http://www.safe.nite.go.jp/english/kizon/ KIZON_start_hazkizon.html. Test details are published in the Official Bulletin of Economy, Trade and Industry (in Japanese only).

− The EU risk assessment report (RAR) that was produced in the framework of EU regulation EEC/793/93 (EU, 1993) for coal-tar pitch and copied into an Annex XV Transitional Dossier under REACH (The Netherlands, 2008). The risk assessment of coal-tar pitch is based on data for the 16 EPA-PAHs (Figure 1). This report includes an overview of bioconcentration factors for fish and mussels, as well as for oligochaetes, polychaetes, crustaceans and insects.

− The database of 1535 data points for 702 chemicals in fish as summarized in the supplementary information for the paper by Arnot et al. (2008). In this paper measured bioconcentration values are compared with values estimated by several quantitative structure-activity relationships (QSARs).

− An assessment of the bioaccumulation data of the 16 EPA-PAHs for fish by Lampi and Parkerton (2008). This document complements the review in the EU risk assessment for coal-tar pitch and identifies preferred values for the PBT4 Working Group of the Technical Committee New and Existing Substances. In 2009 an update of this document (Lampi and Parkerton, 2009) was provided to the European Chemicals Agency (ECHA) in a reaction to their proposal to include coal-tar pitch high temperature on the list of compounds for which authorisation is needed.

− Finally recent or additional literature was scanned in Scopus (http://www.scopus.com) for each individual PAH (identified by substance name or CAS registration number) using the following keywords: bioconcentrat*, bioaccumulat*, uptake, depuration, food-web, trophic, biomagnificat*, BCF*, BAF*, FWMF*, TMF*, BMF*, or BSAF*.

Information from these sources showed considerable overlap, but eventually the data collection resulted in a list of 855 BCF values, reported in 133 references. With a few exceptions (see below), each of these references were consulted individually and the reliability of reported BCF values was examined by using similar criteria as those formulated by Parkerton et al. (2008). These criteria are: 1. (details of) test compound and test organism are clearly described 2. the compound is analysed both in water and in the organism 3. no significant adverse effects are reported 4. the reported BCF reflects steady-state conditions with unambiguous units 4 Persistent, Bioaccumulating and Toxic compounds.

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However, due to different interpretation of the results, the assessment of the studies is not necessarily the same as in the assessment recently submitted to ECHA (Lampi and Parkerton, 2009).

Based on this analysis Klimisch scores (Klimisch et al., 1997) were assigned to each BCF value to indicate the reliability. Data that are generated from studies that comply with or are comparable to published guidelines or are conducted with accepted methods that are described in sufficient detail are rated reliable (validity = 1). Studies that include adequate documentation details, but lack specific details or deviate from guideline requirements are deemed reliable with restrictions (validity = 2). Data are rated as unreliable if key information is lacking or when documentation details reveal unacceptable test performance or methodological flaws (validity = 3). The most common reasons for unreliability are exposure concentrations above water solubility and a clear absence of steady state while steady state BCFs are reported. When insufficient details are provided on critical study aspects data are defined as not assignable (validity = 4). Reasons for assigning a validity of 4 include BCF values being based on total radioactivity (which deems it impossible to distinguish between the concentration of the parent compound and that of its transformation products), uncertainty about the exposure concentration (e.g. exposure concentration reported in graphs only, nominal concentration reported only, exposure via sediment or diet, exposure to oil) or (pre-)exposure duration (e.g. for field collected animals). In addition, two studies (Dunn and Stich, 1976; Rantamäki, 1997) that reported depuration half-lives were scored as not assignable, because information was lacking to calculate BCF values from these half-lives (validity = 4).

In addition to these 4 scores to indicate reliability we added the score 5 for BCF values that were reported in one of our sources (see above), but for which the original publication could not be evaluated. For instance, a small number of references (US-EPA, 1976; Linder, 1982; Hall, 1993) could not be traced and BCF values from these references (as reported in the ECOTOX-database) were assigned a validity of 5 (not evaluated). In addition Veith et al. (1979) refer to unpublished data by Call and Brook (1977). As such data are by definition untraceable this reference was also assigned a validity of 5. It is, however, possible that (part of) these unevaluated data were reported in public literature as well. In the assessment by Lampi and Parkerton (2009) several references are made to reports by EMBSI (EMBSI, 2001; 2005; 2006; 2007c; 2007b; 2007a; 2008a; 2008b; 2009). These reports are not publicly available and thus the BCF values of these references were also assigned a validity of 5.

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3 Results

3.1 Reliability of reported BCF values

For almost 40% of the reported BCF values reliability could not be assigned (validity = 4; see Annex II). The main reason for assigning this validity is given for each BCF value as a reliability remark in Annex II. For the majority of unassignable BCF values this was the result of the BCF being based on total radioactivity.

Those BCF values that were assigned not reliable (invalid due to experimental flaws or design limitations; validity 3) are summarized in Annex I. This was about 25 % of the BCF values. The main reasons for deeming the study unreliable are given as reliability remark in Annex I.

Only 293 BCF values (circa 34 %) were deemed reliable, although in many cases (264) with restrictions (i.e. non-guideline studies, but documented and defensible, validity = 2), because many of these studies were performed before guidelines were established. These 293 BCF values were derived for different types of organisms and are summarized in Table 1.

The remaining few BCF values were not evaluated.

3.2 Additional data

Most of the data (re-)evaluated in the present study were already described in the RAR5 (The Netherlands, 2008). Additional studies are briefly described here.

Landrum and Poore (1988) determined the role of lipid content and temperature in the bioaccumulation of phenanthrene and benzo[a]pyrene by mayfly (Hexagenia limbata). The values for benzo[a]pyrene were reported already in the RAR, but those for phenanthrene were not. The study report includes enough details to rate this study reliable with restrictions (validity = 2). In Table 1 the range of BCF values given from this study is based on fresh weight. When lipid normalization (to 5% lipid content) is applied the range for phenanthrene yields 666 – 2600 L/kg and for benzo[a]pyrene this range yields 3400 – 7800 L/kg.

Hall and Oris (1991) determined BCFs for male and female fathead minnows and for eggs of this species exposed to a concentration series of anthracene for 21 d. Steady water concentrations were maintained, but lipid content was not presented. BCFs were calculated for male and female carcasses individually, and is rated reliable with restrictions (validity = 2).

Weinstein (2001) exposed glochidia of Utterbackia imbecillis to fluoranthene in a flow-through system. Both a steady state (1735) and a kinetic BCF value (1813) is given, which are very similar. This is in agreement with the observed steady state. Also further details provided in the study report are sufficient to rate this study as valid with restrictions (validity = 2).

Schuler et al. (2004) exposed crustacean species (Diporeia spec. and Hyalella azteca) and insect larvae (3rd instar Chironomus tentans) to fluoranthene to determine the influence of exposure concentration on bioaccumulation and compare species specific differences. The study report provides sufficient detail to

5 RAR: Risk Assessment Report, produced in the framework of EU regulation EEC/793/93 (EU, 1993).

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rate this study as valid with restrictions (validity = 2). The exposure concentration appears not to have a big influence, but in contrast to Diporeia spec. the other species are able to metabolise fluoranthene, resulting in higher elimination rates and lower BCF values.

Richardson et al. (2005) conducted semi-batch seawater experiments to follow the uptake and release of anthracene, fluoranthene, pyrene and benzo[a]pyrene, as well as 4 organochlorine pesticides, in semi-permeable membrane devices and green-lipped mussels (Perna viridis). This study was well conducted and appears to yield reliable BCF values based on lipid weight (anthracene: 380000; fluoranthene: 245000; pyrene: 891000; benzo[a]pyrene: 170000). Normalised to a 5% lipid content (ECHA, 2008), these BCF are 19000, 12250, 44550, and 8500, respectively. Lipid weight itself was not given in the study. This study is rated as reliable with restriction (validity = 2).

Wang and Wang (2006) studied the bioaccumulation and transfer of benzo[a]pyrene in a simplified marine food chain. Both dietary and aqueous exposure to benzo[a]pyrene were examined in copepods (Acartia erythraea) and fish (Lutjanus argentimaculatus), but details are not always clear deeming this study unassignable (validity = 4).

Yakata et al. (2006) tested seven organic compounds including acenaphthylene in carp (Cyprinus carpio). The tests were conducted according to OECD Guideline 305 (OECD, 1996), resulting in a BCF for acenaphthylene of 271 L/kg (560 after lipid normalization). Sufficient details were provide to rate this guideline study as reliable (validity = 1).

Jonker and Van der Heijden (2007) determined BCF values for Lumbriculus variegatus in several different test setups. These studies were, however, deemed unreliable (validity = 3), because sediment was present in the test (adding uncertainties to the exposure route) and BCF values were given in graphs only.

In a study by Cheikyula et al. (2008) fish (Paralichthys olivaceus, Pagrus major and Oryzias javanicus) were exposed for ten days to a mixture of 4 PAHs (phenanthrene, pyrene, chrysene and benzo[a]pyrene). The exposure concentration of chrysene in this study appeared to be above the water solubility of this compound, and consequently the mixture as a whole must be oversaturated. So BCF values from this study are not reliable (validity = 3).

Bioavailability of benzo[k]fluoranthene was reported for Oryzias latipes by Chen et al. (2008). From this study a BCF value could only be estimated from concentrations in water and fish that were reported in graphs. In addition the reported exposure concentrations appear to be nominal concentrations (validity = 3).

Grass shrimp larvae were exposed to fluoranthene and benzo[a]pyrene by Weinstein and Garner (2008). The reported BCF values were averages for several exposure concentrations, but information is lacking to examine the validity of this procedure. In addition, BCF values appear to be based on dry weight and the exposure concentration for benzo[a]pyrene appears to be above water solubility (validity = 3).

A rather reliable study in estuarine copepods (Cailleaud et al., 2009), reports dry weight based BCF values for phenanthrene (550), pyrene (900), chrysene (950), benzo(b+k)fluoranthene (1300), and benzo[a]pyrene (1750). These values are only reported in a graph deeming this study as reliable with restrictions (validity = 2). Since no distinction was made between benzo[b]fluoranthene and benzo[k]fluoranthene the value for benzo(b+k)fluoranthene is rated as unassignable (validity 4).

In a study by Takeuchi et al. (2009) biomagnification profiles were elucidated for a range of PAHs, alkylphenols and polychlorinated biphenyls. The molluscs, crustaceans and fish that were examined were collected in the Tokyo Bay, which makes the actual exposure concentrations uncertain (although measured water concentrations were given). However, the reported concentrations in seawater and the

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organisms can be used to calculate bioaccumulation values (BAFs) and thus this study is rated reliable with restrictions (validity = 2). In general 5% lipid normalized BAF values for all species tested are >5000 L/kg for anthracene, fluoranthene, pyrene, benz[a]anthracene, chrysene, benzo[b]fluoranthene, benzo(j+k)fluoranthene, benzo[a]pyrene, indeno[1,2,3-cd]pyrene, and benzo[ghi]perylene, with a few exceptions: in the fish (Acanthogobius flavimanus) BAF values are lower for anthracene (4527), fluoranthene (629), pyrene (1010), and indeno[1,2,3-cd]pyrene (4167), and in the crustacean (Hemigrapsus penicillatus) BAF values are lower for anthracene (4026) and fluoranthene (1713). For phenanthrene the values fall within the 2000 – 5000 L/kg range, with the mollusc Mytilopsis sallei (BAF: 1781), the crustacean (BAF: 776) and the fish (BAF: 1019) as exceptions. Because these values cannot be directly compared with BCF values, the BAF values are not included in Table 1.

3.3 Evaluation of reliable BCF values

From Table 1 it can be concluded that BCF values are low for naphthalene (in fish: 66 – 999 L/kg; in crustaceans: 131 – 736 L/kg), acenaphthene (in fish: 735 – 760 L/kg), acenaphthylene (in fish: 271 – 387 L/kg) and 9H-fluorene (in fish: 590 – 1467 L/kg; in Daphnia magna: 506 L/kg; in Lumbriculus variegatus: 400 L/kg).

In aquatic plants (Lemna gibba) this holds for all PAHs tested (anthracene: 4 – 28 L/kg; phenanthrene: 11 – 92 L/kg; benzo[a]pyrene: 7 – 910 L/kg). Also polychaetes (Nereis virens) do not highly accumulate the PAHs tested (BCF values for phenanthrene, fluoranthene and pyrene are all below 1000 L/kg).

Anthracene is clearly accumulated. Both for carp (Cyprinus caprio) and for fathead minnows (Pimephales promelas) BCF values are reported above 2000 L/kg. For female fathead minnows, the highest BCF (4973 L/kg) is even close to the very bioaccumulative (vB) limit of 5000 L/kg. Hall and Oris (1991) argue that this may be due to a higher lipid content in females, but unfortunately they did not measure lipid content in the fish. The only study that reports lipid content in Pimephales promelas (Carlson et al., 1979) does not distinguish between males and females, but their highest reported lipid content value is 4.8 ± 1.5 % (average ± SD). Assuming that the females are in the higher region of this range (i.e. around 6%), the lipid normalized BCF value will be around 4100. For the amphipod Pontoporeia hoyi the BCF is (far) above this limit (16800 – 40000 L/kg) and also the polychaete Stylodrilus heringianus show a high BCF value for anthracene (5206 L/kg).

For phenanthrene BCF values are reported above 2000 L/kg for sheepshead minnows (Cyprinodon variegatus; 2229 L/kg) and fathead minnows (Pimephales promelas; BCFK: 3611 L/kg). For both species also values below 2000 L/kg are reported, but for fathead minnows also a final BCF value of 5100 L/kg is reported on day 28, although concentrations in fish appear to decrease over the period from day 18 to 28 of the uptake phase. In molluscs phenanthrene is accumulating, but BCF levels remain well below 2000 L/kg (maximum: 1280 L/kg). In crustaceans BCF values are generally very high (cf. Diporeia spp. and Pontoporeia hoyi >5000 L/kg), but low values are also reported (cf. Daphnia sp. and Crangon septemspinosa: 210 – 325 L/kg). Whether these differences are due to differences between species is difficult to judge, since other experimental settings (e.g. exposure time) also differ. For insects (Hexagenia limbata) BCFs clearly depend on lipid content of the organism, but on average values are above 2000 L/kg. For oligochaetes (Stylodrilus heringianus) the BCF for phenanthrene is 5222 L/kg.

Fluoranthene does accumulate in fish (Pimephales promelas; kinetic BCF calculated from the presented data: 2439). The uptake curve does not fit well to a first order kinetic model. This is mainly because the concentrations in fish are remarkably lower at 28 days than at 4, 7, 14, and 21 days. Static

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BCF values at these time intervals are 2275, 3265, 2962, and 3443, respectively. In contrast, the static BCF at 28 days is only 1507 – 1884. In juvenile fish, fluoranthene accumulation may be significant, e.g. Cho et al. (2003) reported a kinetic BCF of 14839, although exposure in this experiment was very short (24 h, followed by 24 h depuration phase) and the value may be based on dry weight (study validity = 4). In molluscs (Mya arenaria and Mytilus edulis) fluoranthene is clearly accumulating and also in some crustaceans (Diporeia spp. and Hyalella azteca) fluoranthene shows very high BCF values. The low BCF value for Crangon septemspinosa is likely species specific, since this species generally shows lower BCF values in comparison with other invertebrates (cf. McLeese and Burridge, 1987). For insects (Chironomus tentans larvae) BCF values for fluoranthene are around 2000 L/kg. Fluoranthene is also the only PAH tested on an amphibian (Rana pipiens), but for this species BCF values are (far) below 2000 L/kg.

Based on Table 1 BCF values for pyrene in fish are lower than 2000, most likely because it is metabolized and subsequently excreted. For a study with fathead minnows (Carlson et al., 1979) the BCFK was estimated as 1279 L/kg. As with fluoranthene, however, these data appear to deviate from first order kinetics. The concentrations in fish after 28 d are much lower than those after 14 or 21 days, resulting a much lower BCFss after 28 d (785 L/kg) than the ones reported after 14 and 21 days (2300 and 2600 L/kg respectively). Yet, in a recent field study (Takeuchi et al., 2009) pyrene was not highly accumulating (BAF: 1010), supporting the non-bioaccumulative behaviour of pyrene in fish. Also insects (Chironomus riparius larvae) do not highly accumulate pyrene (Wildi et al., 1994). In molluscs, however, BCF values are generally (far) above 5000 L/kg, which is only partly due to their relatively high lipid content (cf. Bruner et al., 1994; Baussant et al., 2001a). In crustaceans (Diporeia spp., Pontoporeia hoyi) BCF values are also very high. Only Cragon septemspinosa shows again a low BCF value (see also the results for fluoranthene). The oligochaete Stylodrilus heringianus shows a very high BCF for pyrene (6688), but for Lumbriculus variegatus the BCF is much lower (1720).

Benz[a]anthracene hardly accumulates in fish (Pimephales promelas) but in crustaceans BCF values are very high (>10000).

Benzo[a]pyrene shows similar patterns with fish hardly accumulating and invertebrates that do so significantly, with the exception of Chironomus riparius that is capable of metabolizing benzo[a]-pyrene (Leversee et al., 1981; 1982).

For chrysene, benzo[k]fluoranthene, benzo[ghi]perylene and dibenz[a,h]anthracene only for Daphnia magna valid data are available, showing very high BCF values for all compounds.

For benzo[b]fluoranthene and indeno[1,2,3-cd]pyrene no reliable data are available at all, although these compounds appear to accumulate in molluscs in the field (Takeuchi et al., 2009).

Table 1. Overview of reliable BCF values.

Species Test Systema)

Chem. analysisb)

BCF (L/kg) Typec) Vd) Ref.e)

Naphthalene Pisces Cyprinodon variegatus FT GCMS 895, 999 1) Kin. 1 [12] Cyprinus carpio FT GC 66, 76 1) Equi. 2 [26] Lepomis macrochirus FT 14C 300 Kin. 2 [20]

Crustacea Daphnia pulex S Flu.Spec. 131 Equi. 2 [31] Diporeia spp. SR 14C 311, 459, 736 1) Kin. 2 [15]

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Species Test Systema)

Chem. analysisb)

BCF (L/kg) Typec) Vd) Ref.e)

Acenaphthene Pisces Cyprinus carpio FT HPLC 735, 760 1) Equi. 2 [27]

Acenaphthylene Pisces Cyprinus carpio FT HPLC 385, 387 1) Equi. 2 [28]

FT HPLC 271 Equi. 1 [34] 9H-fluorene Pisces Cyprinus carpio FT GCMS 590, 637 1) Equi. 2 [29] Pimephales promelas FT HPLC 1112, 1459 1) Kin. 2 [4]

Crustacea Daphnia magna SR HPLC 506 Equi. 2 [23]

Oligochaeta Lumbriculus variegatus SR HPLC 400 Equi. 2 [1]

Anthracene Pisces Cyprinus carpio FT GCMS 1890, 2225 1)

2545, 1960 2) Equi. Kin.

2 [25]

Pimephales promelas (eggs) FT HPLC 563 – 966 1) Equi. 2 [10] Pimephales promelas (male) FT HPLC 1126, 2476 1) Equi. 2 [10] Pimephales promelas (female) FT HPLC 3581, 4973 1) Equi. 2 [10]

Mollusca Perna viridis SR GC 19000 3) Equi. 2 [24]

Crustacea Daphnia magna SR HPLC 970 Equi. 2 [23] Daphnia pulex S Flu.Spec. 917 Equi. 2 [31] Hyalella azteca FT 14C 1800 Equi. 2 [14] Pontoporeia hoyi FT 14C 16800 Kin. 2 [16] FT 14C 39727 Kin. 1 [17]

Oligochaeta Lumbriculus variegatus SR HPLC 1370 Equi. 2 [1] Stylodrilus heringianus FT 14C 5206 Kin. 2 [8]

Magnoliophyta Lemna gibba S 14C 4 – 28 1) Kin. 2 [6]

Phenanthrene Pisces Cyprinodon variegatus FT GCMS 810, 2229 1) Kin. 1 [12] Pimephales promelas FT HPLC 2050 – 5100 1)

2086 – 3611 4) Equi. Kin.

2 2

[4]

Mollusca Mya arenaria FT HPLC 1280 Kin. 1 [21] Mytilus edulis FT HPLC 1240 Kin. 1 [21]

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Species Test Systema)

Chem. analysisb)

BCF (L/kg) Typec) Vd) Ref.e)

Crustacea Crangon septemspinosa FT HPLC 210 Kin. 1 [21] Daphnia magna SR HPLC 324 Equi. 2 [23] Daphnia pulex S Flu.Spec. 325 Equi. 2 [31] Diporeia spp. SR 14C 5513 – 11440 1) Kin. 2 [15] Eurytemora affinis GCMS 550 5) Equi. 2 [3] Pontoporeia hoyi FT 14C 28043 Kin. 1 [17]

Insecta Hexagenia limbata FT 14C 493 – 5697 6) Kin. 2 [13]

Oligochaeta Stylodrilus heringianus FT 14C 5222 Kin. 2 [8]

Polychaeta Nereis virens FT HPLC 500 Kin. 1 [21]

Magnoliophyta Lemna gibba S 14C 11 – 92 1) Kin. 2 [6]

Fluoranthene Pisces Pimephales promelas FT HPLC 2439 Equi. 2 [4]

Mollusca Mya arenaria FT HPLC 4120 Kin. 1 [21] Mytilus edulis FT HPLC 5920 Kin. 1 [21] Perna viridis SR GC 12250 3) Equi. 2 [24] Utterbackia imbecillis (glochidia) FT HPLC 1735,

1813 Equi., Kin.

2 [32]

Crustacea Crangon septemspinosa FT HPLC 180 Kin. 1 [21] Daphnia magna SR HPLC 1742 Equi. 2 [23] Diporeia spp. SR 14C 15136 – 58884 1) Kin. 2 [30] Hyalella azteca SR 14C 1202 – 5370 1) Kin. 2 [30]

Insecta Chironomus tentans (3rd instar larvae)

SR 14C 891 – 2512 1) Kin. 2 [30]

Polychaeta Nereis virens FT HPLC 720 Kin. 1 [21]

Amphibia Rana pipiens FT HPLC 611 – 1659 1) Equi. 1 [22]

Pyrene Pisces Cyprinodon variegatus FT GCMS 97, 145 1) Kin. 1 [12] Pimephales promelas FT HPLC 1297 Kin. 2 [4]

Mollusca Dreissena polymorpha S 3H 13000 – 35000 6) Kin. 2 [2] S 3H 22000 – 77000 7) Kin. 2 [9] Mya arenaria FT HPLC 6430 Kin. 1 [21] Mytilus edulis FT HPLC 4430 Kin. 1 [21] Perna viridis SR GC 44550 3) Equi. 2 [24]

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Species Test Systema)

Chem. analysisb)

BCF (L/kg) Typec) Vd) Ref.e)

Crustacea Crangon septemspinosa FT HPLC 225 Kin. 1 [21] Daphnia magna SR HPLC 2702 Equi. 2 [23] Daphnia pulex S Flu.Spec. 2702 Equi. 2 [31] Diporeia spp. SR 14C 12300 – 36333 1) Kin. 2 [15] Eurytemora affinis GCMS 900 5) Equi. 2 [3] Pontoporeia hoyi FT 3H 166000 Kin. 1 [17]

Insecta Chironomus riparius (larvae) S 14C 713 – 1227 8) Equi. 2 [33]

Oligochaeta Lumbriculus variegatus SR HPLC 1720 Equi. 2 [1] Stylodrilus heringianus FT 3H 6688 Kin. 2 [8]

Polychaeta Nereis virens FT HPLC 700 Kin. 1 [21]

Benz[a]anthracene Pisces Pimephales promelas FT HPLC 260 Equi. 2 [5]

Crustacea Daphnia magna SR HPLC 10226 Equi. 2 [23] Daphnia pulex S Flu.Spec. 10109 Equi. 2 [31] Pontoporeia hoyi FT 14C 63000 Kin. 1 [17]

Chrysene Crustacea Daphnia magna SR HPLC 6088 Equi. 2 [23] Eurytemora affinis GCMS 950 5) Equi. 2 [3]

Benzo[a]pyrene Pisces Lepomis macrochirus FT 14C 367 – 608 9) Kin. 2 [11] FT 14C 30 Kin. 2 [20]

Mollusca Dreissena polymorpha S 3H 41000 – 84000 6) Kin. 2 [2] S 3H 24000 – 273000 7) Kin. 2 [9] Perna viridis SR GC 8500 3) Equi. 2 [24]

Crustacea Daphnia magna SR HPLC 12761 Equi. 2 [23] S 14C 2837 Equi. 2 [18] Eurytemora affinis GCMS 1750 5) Equi. 2 [3] Mysis relicta FT 3H 8496 Kin. 2 [7] Pontoporeia hoyi FT 14C 73000 Kin. 1 [17] FT 3H 48582 Kin. 2 [7]

Insecta Chironomus riparius (4th instar larvae)

S 14C 650 Equi. 2 [19]

S 14C 166 Equi. 2 [18] Hexagenia limbata FT 3H 2725 – 11167 6) Kin. 2 [13]

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Species Test Systema)

Chem. analysisb)

BCF (L/kg) Typec) Vd) Ref.e)

Oligochaeta Stylodrilus heringianus FT 3H 7317 Kin. 2 [8]

Magnoliophyta Lemna gibba S 14C 7 – 910 1) Kin. 2 [6]

Benzo[k]fluoranthene Crustacea Daphnia magna SR HPLC 13225 Equi. 2 [23]

Benzo[ghi]perylene Crustacea Daphnia magna SR HPLC 28288 Equi. 2 [23]

Dibenz[a,h]anthracene Crustacea Daphnia magna SR HPLC 50119 Equi. 2 [23]

a) FT: flow-through system; S: static; SR: static renewal. b) 14C: radioactive carbon in the parent compound; GC: Gas chro-matography; GCMS: Gas chromatography with mass spectrometry; Flu.Spec.: fluorescence spectrometry; 3H: radioactive hydrogen in the parent compound; HPLC: high pressure liquid chromatography. c) Kin.: Kinetic BCF, i.e. k1/k2; Equi.: BCF at (assumed) equilibrium, i.e. Corganism/Cwater. d) V: validity; 1: valid without restrictions; 2: valid with restrictions. e) References: [1] (Ankley et al., 1997); [2] (Bruner et al., 1994); [3] (Cailleaud et al., 2009); [4] (Carlson et al., 1979); [5] (De Maagd et al., 1998); [6] (Duxbury et al., 1997); [7] (Evans and Landrum, 1989); [8] (Frank et al., 1986); [9] (Gossiaux et al., 1996); [10] (Hall and Oris, 1991); [11] (Jimenez et al., 1987); [12] (Jonsson et al., 2004); [13] (Landrum and Poore, 1988); [14] (Landrum and Scavia, 1983); [15] (Landrum et al., 2003); [16] (Landrum, 1982); [17] (Landrum, 1988); [18] (Leversee et al., 1981); [19] (Leversee et al., 1982); [20] (McCarthy and Jimenez, 1985); [21] (McLeese and Burridge, 1987); [22] (Monson et al., 1999); [23] (Newsted and Giesy, 1987); [24] (Richardson et al., 2005); [25] (RIITI, 1977); [26] (RIITI, 1979); [27] (RIITI, 1990a); [28] (RIITI, 1990b); [29] (RIITI, 1990c); [30] (Schuler et al., 2004); [31] (Southworth et al., 1978); [32] (Weinstein, 2001); [33] (Wildi et al., 1994); [34] (Yakata et al., 2006) 1) Values represent (a range of) BCF values from (a range of) different exposure concentrations. 2) Kinetic model with estimated uptake rate constant based on fish size applied to the data, high and low concentration, respectively. 3) In this study BCF values are based on lipid weight, values given in this table are normalized to 5% lipid content. 4) Kinetic value based on the presented data. However, the uptake curve for phenanthrene does not show the regular levelling off in time. Therefore, static BCF values at the end of 28 d do exceed 5000. 5) BCFs are based on dry weight. 6) BCFs were determined with test animals that differ in lipid content. 7) BCFs were determined at different exposure temperatures. 8) BCFs were determined at different exposure pHs. 9) BCFs were determined at different feeding regimes, i.e. fed both during uptake and depuration, not fed during uptake but fed during depuration.

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4 Discussion In the Risk Assessment Report (RAR) on coal-tar pitch, high temperature (The Netherlands, 2008) and in the assessment by Lampi and Parkerton (2009) validity was also assigned to the different BCF studies. In the present report the re-evaluation of the studies resulted in different validity scores in comparison to these references which are discussed below.

4.1 Evaluating the bioaccumulation assessment by Lampi and Parkerton

In a study by De Voogt et al. (1991) BCFs were calculated for 9H-fluorene, anthracene and pyrene, based on 7-day semi-static renewal bioaccumulation tests with guppy (Poecilia reticulata). In the RAR (The Netherlands, 2008) these BCF were assigned a validity of 2 (valid with restrictions), but Lampi and Parkerton (2009) argue that many details on test set-up and results (e.g. whether fish are fed or not, measured water concentrations) are lacking from the paper, so they rate these values not assignable (validity = 4). De Voogt et al. (1991) also report BCF values from 48-hour static exposures. Our re-evaluation of this source showed some inconsistencies within the study and thus reliability of the reported BCF could not be assigned (validity 4). First, the static renewal study with renewal every 12 h showed a steady state BCF for pyrene at 48 h of 11300 L/kg, which is extraordinarily high, even considering the high lipid content of 9%. However, in the static Banerjee method during 48 h, with correction for loss due to volatilisation and sorption in controls, the BCF was 4810 L/kg. Analysis of the fish was only performed at the end of this 48 h period. The amount of pyrene in fish was only 62% of that estimated from the loss of the water phase. The remaining 38% might be attributed to metabolism, which would yield a BCF value of circa 3000 L/kg. The elimination of pyrene from fish was followed as well during 6 days after the static exposure had ended. This yielded an elimination rate constant of 0.66 d-1. With the estimated rate constant from the static uptake phase this would yield a BCF value of 4863 L/kg. However, the uptake rate constant estimated by the Banerjee method is remarkably high, even considering the small size of the fish (135 mg). If the uptake rate constant would be estimated from the fish size (ECHA, 2008), similar to what is done in the dietary bioaccumulation tests (see section 4.3), the BCF would only be 1485 L/kg. The results from this study are therefore rather inconclusive (validity 4).

For similar reasons the short-term BCF values as reported in De Maagd (1996) were rated as unreliable (validity = 3) by Lampi and Parkerton (2009). However, the BCF values from De Maagd (1996) were derived kinetically with the adjusted Banerjee method, in which not only the decrease in the water concentration is monitored but the increase in the concentration in fish as well. Additional measure-ments were done with piperonyl butoxide added to the water to stop metabolism in the fish by inhibiting the cytochrome P450 isoenzymes. The test duration is very short and induction of metabolization may occur if fish are exposed for a prolonged period. Yet, for benz[a]anthracene De Maagd et al. (1998) found that the exposure time did not influence the metabolic rate. This substance, however, is metabolized to a large extent by fish and for the PAHs that are less easily metabolised, induction may still be an important process. The BCF values from De Maagd (1996) for anthracene, phenanthrene and fluoranthene are indeed higher than values obtain from studies with the same species but a longer exposure time, with constant exposure over time (Carlson et al., 1979; Hall and Oris, 1991), but still within a factor of 1 to 3. Therefore, the results from De Maagd (1996) should be considered with care, but are still important as circumstantial evidence in a weight of evidence approach to decide on the bioaccumulation potential of the studies PAHs.

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Further, Lampi and Parkerton (2009) state that the water concentrations of several PAHs as used by De Maagd (1996) approach the LC50. However, such LC50 values can only be obtained by irradiation with ultraviolet light, such that the PAHs exert phototoxic effects. Under normal laboratory conditions with gold or cool white fluorescent lighting or similar, under which BCF studies are performed, such phototoxic effects will not occur. Most PAHs are not acutely toxic to fish up to their limit of solubility under such conditions.

Values for benz[a]anthracene as reported by De Maagd et al. (1998) were rated as unassignable by Lampi and Parkerton (2009), in contrast with the rating in the RAR (validity = 2). This appears to be based on the absence of lipid data only, which in our opinion is not sufficient for rating a study as unassignable. We therefore still support the rating from the RAR (validity = 2).

A study by Weinstein and Oris (1999) with larval fathead minnows reports a BCF for fluoranthene of 9054. This value, however, is based on dry weight, which makes it difficult to compare with BCF values based on wet weight. Lampi and Parkerton (2009) assigned the study as unassignable (validity = 4), which we consider justified given the uncertainties regarding the expression of the concentration. Assuming a water content of 75 – 85%, which is not uncommon in fish, the BCF will be 1358 – 2264 based on wet weight. In addition, it might be assumed that this value is an overestimation for the larger fish regularly used in bioconcentration tests, because biotransformation systems in larvae are not yet fully developed, although for the same species a BCF of 2439 was derived from a 28-day study with fish that were 5 to 6 weeks old (Carlson et al., 1979).

Another study with larval fathead minnows (Cho et al., 2003) was rated reliable (validity = 1) in the RAR. Lampi and Parkerton (2009) rated the same study as unreliable (validity = 3), based on the absence of reported units for BCF, the absence of reported lipid content, the test concentration being close to LC50, and uncertainty about whether the BCF is based on dry weight or wet weight. In our opinion these reasons just rate this value as unassignable due to a lack of information provided (validity = 4). Moreover, given the fact that an earlier publication from this group (Weinstein and Oris, 1999) are based on dry weight and for the analysis a reference is made to this publication, it seems plausible to assume that BCF values are on a dry weight basis. With the same assumptions as above for the dry weight content, BCF values on wet weight basis of 2225 – 3709 are calculated, in the presence of 40 µg/L methyl-tert-butyl ether the range is 4381 – 7302. With respect to toxicity, it should be noted that fluoranthene is only acutely toxic to fish at the used concentrations in the presence of UV-lighting and certainly not under laboratory lighting.

From a study by Finger et al. (1985) in which bluegills are exposed to 9H-fluorene for 30 days exposure concentrations and internal fish concentrations could be derived. These values were based on dry weight and Lampi and Parkerton (2009) rated the study as unassignable (validity = 4), which is agreed upon. Using the highest reported value (1800) and assuming a water content of 75 – 85%, the BCF will be 270 – 450 based on wet weight.

Baussant et al. (2001a; 2001b) reported BCF values for several PAHs based on studies in which turbots were exposed to crude oil. Due to the absence of reported fish and water concentrations these BCF values were rated as unassignable by Lampi and Parkerton (2009). Exposure concentrations, are however given in a figure, and although these values did not exceed water solubility, the test was performed using a dispersed crude oil. Consequently, the solution is oversaturated and BCF values are rated unreliable (validity = 3) instead of unassignable. A depuration phase was also reported in these studies. The half-lives for naphthalene, fluorene, phenanthrene and chrysene were remarkably constant, varying only between 14 and 29 hours. With the uptake rate constant estimated from fish size (see section 4.3), BCF values of 196 to 407 are calculated for these compounds. However, the lack of differentiation in the BCF values for the studied PAHs is not in accordance with other studies. Possibly, the use of saturated concentrations leads to high fish concentrations of total PAH, such that interference

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of the different single PAHs can not be excluded. Therefore, these results should be considered as unassignable (validity =4).

A study by Carlson et al. (1979) reports BCF results for fathead minnows exposed to a series of PAHs via flow-through conditions for 28 d, followed by a 5 d depuration phase. Although this is not a guideline study, enough details are provided to rate this study as reliable with restrictions (validity = 2). Instead of using the reported BCF values for day 28 we calculated kinetic BCF values based on the reported fish and water concentrations to minimize variability. Lampi and Parkerton (2009) indicated that phenanthrene exposures in one exposure (experiment 2, tank #1) are unreliable, because of declining water concentrations during the 28 d exposure. In addition they assign the results from another exposure (experiment 2, tank#2) reliable only up to 10 days (averaging reported BCFss values for days 7 and 10), considering data later in the experiment as unreliable ‘due to lack of steady state, and fluctuating test concentrations’. We agree that in this experiment a steady state is lacking, but in our opinion the test concentrations in this study do not fluctuate too much. Using the average BCFss value of the last three reported values (day 18, 25 and 28; resulting in a BCF value of 4300) appears more reasonable than the approach by Lampi and Parkerton.

4.2 Evaluating the bioaccumulation assessment in the RAR

Freitag et al. (1982; 1985) report steady state BCF values for golden ide (Leuciscus idus melanotus) exposed to different PAHs for 3 d. In the RAR these studies are rated unassignable (validity = 4). The exposure, however, is static for 3 days, which deems it unlikely that a steady state has been established. In addition, no aeration of the water column was provided, suggesting additional stress for the fish and deeming these studies unreliable (validity = 3).

Barrows et al. (1980) report a reliable study on the accumulation of acenaphthene in bluegill sunfish (Lepomis macrochirus) (RAR: validity = 2). Unfortunately, concentrations were based on total radioactivity and since biotransformation can be expected this study is rated unassignable (validity = 4).

Also the study by Weinstein and Polk (2001), which reports BCF values for Utterbackia imbecillis glochidia exposed to anthracene and pyrene is a very good study (RAR: validity = 2) with one major flaw: BCF values are based on dry weight, resulting in very high values and complicating comparisons with BCF values based on wet weight (validity = 4). In general, however, BCFs in this study are low. Assuming a water content of 75 – 85% the highest value for anthracene (420) would result in a wet weight BCF of 63 – 105, and for pyrene this value (1229) would result in a wet weight BCF of 184 – 307.

McCarthy and Jimenez (1985) report both a kinetic and a steady state BCF for bluegill sunfish (Lepomis macrochirus) after a 2 d benzo[a]pyrene exposure, followed by a 4 d depuration phase In the RAR these values are rated valid with restrictions (validity = 2). In this re-assessment, the short exposure time and the presence of humic material in some of the tests, and the high fish loading should rate these values as unreliable (validity = 3), especially since these values are based on total radioactivity. A correction for parent substance in fish between 16 and 32 hours of the uptake phase is not accurate but would indicate a BCF value well below 100 for benzo[a]pyrene. The results for naphthalene, without added humic material, can be considered as more reliable as it was shown that naphthalene was not metabolized to a significant degree.

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4.3 Dietary bioaccumulation studies

Lampi and Parkerton (2009) underline the importance of dietary exposure scenarios, especially for the more lipophilic PAHs. Although we agree with their views in this respect, the available data that could be evaluated were restricted to two studies (Niimi and Palazzo, 1986; Niimi and Dookhran, 1989). Other dietary studies only appear to be done by EMBSI (EMBSI, 2001; 2005; 2006; 2007c; 2007b; 2007a; 2008a; 2008b), which could not be evaluated for this study (validity = 5).

For the dietary studies that could be evaluated, Lampi and Parkerton (2009) give half-lives (t0.5) and normalized BCF values. These BCF values are calculated based on the following two equations (ECHA, 2008):

2

15.01 )2ln( k

ktkBCF =⋅=

and

32.01 W)520( −⋅=k

in which: k1 = uptake rate (ml/gwet weight/day); k2 = elimination rate (/day); W = fish wet weight (g); t0.5 = growth-corrected half-life in fish (days).

With the weight of the fish at the beginning of the depuration phase (estimated from the values presented during the depuration phase) of 658 g (Niimi and Palazzo, 1986), BCF values were estimated to be 645 for fluorene, 847 for phenanthrene, 672 for anthracene, 582 for fluoranthene, 286 for benzo[a]pyrene, and 356 for benz[a]anthracene. Values for phenanthrene, anthracene and fluoranthene are remarkably lower than from studies with aqueous exposure (Table 1). For the study with acenaphthylene (Niimi and Dookhran, 1989) a weight of 250 g is reported and a BCF of 139 can be calculated from the presented data.

These values differ from the values reported by Lampi and Parkerton (2009) and the reason for these differences could not be produced, even if other weight assumptions were applied. For instance, for phenanthrene Niimi and Palazzo reported a growth corrected depuration rate (k2 = t0.5/0.693) of 0.077 (d-1), resulting in a t0.5 of 9 d (in agreement with Lampi and Parkerton). The calculated k1 depends on the fish weight. Niimi and Palazzo reported a weight range of 651 ± 132 to 875 ± 141 g, resulting in a k1 range of 57 – 70 (using 1016 and 519 g as weights). These values would result in a BCF range of 738 – 915. When these values are normalized to a fish with 5% lipid content (using the lipid content of 8% as reported in Lampi and Parkerton, although no lipid content is indicated in the Niimi and Palazzo study) this results in a range for the normalized BCF of 461 – 572, while a normalized BCF of 407 is reported by Lampi and Parkerton (2009). Similar differences were found for the other compounds from the Niimi and Palazzo study, which suggests that the calculations in Lampi and Parkerton (2009) are not as straightforward as indicated in that report.

Further, very low BCF values are reported by Lampi and Parkerton (2009) for chrysene and pyrene based on the study by Niimi and Palazzo (1986). This was based on the fact that these compounds were not detected at all in fish tissues and the assumption that this could be attributed to low half-lives of less than 2 days. However, this assumption could be incorrect, because the absence of the compounds in the fish tissue may be fully attributable to a very low absorption efficiency. This is also indicated in a subsequent paper (Niimi and Dookhran, 1989), where the same was observed for the PAHs dibenz[a,h]anthracene and benzo[ghi]perylene.

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In addition, the reported BCF values from dietary studies in Lampi and Parkerton (2009) show other oddities, e.g. the data for benz[a]anthracene, pyrene and benzo[a]pyrene from the EMBSI 2005 study show the same BCF value for all compounds, which is highly unlikely.

Due to the uncertainties in calculating BCF values from the evaluated dietary studies (Niimi and Palazzo, 1986; Niimi and Dookhran, 1989) and the fact that the study reports from EMBSI could not be evaluated at all, in the present report BCF values based on dietary studies were not considered in the assessment of bioaccumulation of PAHs.

4.4 Using bioaccumulation data for regulatory purposes

In regulatory frameworks BCFs values are usually considered as a measure for the biomagnification potential of a certain compound. As stated before in the introduction, several factors influence the level of biomagnification of a compound, which may result in situations where at lower trophic levels bioaccumulation and biomagnification takes place, while higher in the food chain organisms are capable of handling the compound and efficiently excreting it (e.g. Wang and Wang, 2006; Wan et al., 2007; Nfon et al., 2008; Takeuchi et al., 2009).

According to the European REACH legislation, ‘the assessment of bioaccumulation shall be based on measured data on bioconcentration in aquatic species’ (EU, 2007). When data are available for several aquatic species (preferably from several levels within a food chain) all these data should be taken into account. It might be argued that in this case it appears to make sense to take a weight-of-evidence approach in which (reliable) information from fish (which are higher in the food chain and serve as food for mammals, including humans, and birds) add more weight to an assessment of biomagnification than information on e.g. daphnids (lower in the food chain), although it cannot be excluded that bioaccumulation in the lower food chain may result in effects higher up in the food chain that are not directly related to internal concentrations. In addition, although mussels are relatively low in the food chain, (reliable) results from mussel studies, may add more weight to a biomagnification assessment than data on daphnids, because mussels serve as food for mammals and birds as well.

Recently the European Chemicals Agency (ECHA) published an Annex XV Report proposing coal-tar pitch, high temperature, for identification of a substance as a CMR, PBT, vPvB or substance of equivalent level of concern. Part of this report is an assessment of the aquatic bioaccumulation of this substance, which is based on the bioaccumulation potential of the 16 EPA-PAHs. This assessment is solely based on data that were published in the RAR (The Netherlands, 2008). As argued above (see sections 4.1 and 4.2), the present re-evaluation of bioaccumulation data resulted in conflicts with the conclusions from the RAR, which may result in a different conclusion on the PBT/vPvB assessment for the individual PAHs, but not for coal-tar pitch, high temperature as a substance and other substances for which such an assessment is based on PAHs, considering the fact that at least some of the substances that can regarded as PBT and/or vPvB are present in amounts amply exceeding 0.1%.

ECHA did not assess the bioaccumulation potential of naphthalene, acenaphthene, acenaphthylene, and 9H-fluorene, as these were not detected in coal-tar pitch high temperature in concentrations exceeding 0.1%. Anthracene was deemed bioaccumulative (B: BCF 2000 – 5000) and each of the other EPA-PAHs were deemed very bioaccumulative (vB: BCF >5000), although only for fluoranthene and pyrene this was based on fish data. For the other PAHs the vB status was based on invertebrates.

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Table 2. Summary of highest reliable BCF values for the 16 EPA-PAHs.

Substance BCF value (WW)

BCF value (5% lipid norm.) a)

Species Type b) Reference c)

Naphthalene1) 999 515 Cyprinodon variegatus (Fish) Kin. [6] Acenaphthene1) 760 1000 Cyprinus carpio (Fish) Equi. [10] Acenaphthylene1) 387 509 Cyprinus carpio (Fish) Equi. [11] 9H-fluorene1) 1459 1658 Pimephales promelas (Fish) Kin. [1] Anthracene 4973 –2) Pimephales promelas (Fish) Equi. [4] –3) 19000 Perna viridis (Mollusc) Equi. [9] 39727 210984) Pontoporeia hoyi (Crustacean) Kin. [7] Phenanthrene 3611 4751 Pimephales promelas (Fish) Kin. [1] 28043 148934) Pontoporeia hoyi (Crustacean) Kin. [7] Fluoranthene 2439 2772 Pimephales promelas (Fish) Kin. [1] –3) 12250 Perna viridis (Mollusc) Equi. [9] 58884 –5) Diporeia spec. (Crustacean) Kin. [12] Pyrene 1297 1474 Pimephales promelas (Fish) Kin. [1] –3) 44550 Perna viridis (Mollusc) Equi. [9] 166000 881574) Pontoporeia hoyi (Crustacean) Kin. [7] Benz[a]anthracene 260 –6) Pimephales promelas (Fish) Equi. [2] 63000 334574) Pontoporeia hoyi (Crustacean) Kin. [7] Chrysene 6088 –7) Daphnia magna (Crustacean) Equi. [8] Benzo[a]pyrene 608 –8) Lepomis macrochirus (Fish) Kin. [5] 1910009) 119375 Dreissena polymorpha (Mollusc) Kin. [3] 73000 387684) Pontoporeia hoyi (Crustacean) Kin. [7] Benzo[b]fluoranthene – – No experimental data available – – Benzo[k]fluoranthene 13225 –10) Daphnia magna (Crustacean) Equi. [8] Benzo[ghi]perylene 28288 –11) Daphnia magna (Crustacean) Equi. [8] Dibenz[a,h]anthracene 50119 –12) Daphnia magna (Crustacean) Equi. [8] Indeno[1,2,3-cd]pyrene – – No experimental data available – – a) BCF values are normalized to organisms with a lipid content of 5%. b) Kin.: kinetic BCF value (k1/k2); Equi. BCF value at (assumed) equilibrium (Corganism/Cwater). c) [1] (Carlson et al., 1979); [2] (De Maagd et al., 1998); [3] (Gossiaux et al., 1996); [4] (Hall and Oris, 1991); [5] (Jimenez et al., 1987); [6] (Jonsson et al., 2004); [7] (Landrum, 1988); [8] (Newsted and Giesy, 1987); [9] (Richardson et al., 2005); [10] (RIITI, 1990a); [11] (RIITI, 1990b); [12] (Schuler et al., 2004). 1) For these compounds invertebrates showed lower BCF values than fish, so only fish data are given. 2 In this study no lipid content was given, but based on lipid contents in fathead minnows reported by Carlson et al. (1979) lipid content is expected to be 5 – 6 %, which would result in lipid normalized values ranging from 4100 – 5000. 3) In this study only lipid-based BCF values were given, but lipid content itself was not reported. 4) In this study lipid content was expressed only as percentage of dry weight (35%). In addition the ratio between total wet weight and dry weight was given (0.269). For lipid normalization it was assumed that the same ratio holds for lipids, resulting in a lipid content of 9.4% based on wet weight. 5) In this study no lipid content was given, but for a lipid normalized value to fall below the trigger value of 5000 the lipid content needs to be 59%, which seems to be unrealistically high. 6) In this study no lipid content was given, but for a lipid normalized value to exceed the trigger value of 2000 the lipid content needs to be 0.65%, which seems to be unrealistically low. 7) In this study no lipid content was given, but Liu et al. (1996) report lipid contents in Daphnia magna ranging from 4 – 6%, suggesting that a lipid normalized BCF value will be similar to the wet weight value. If the lipid content is higher than 6.1%, the normalized BCF value will be below 5000. 8) In this study no lipid content was given, but for a lipid normalized value to exceed the trigger value of 2000 the lipid content needs to be 1.5%, which seems to be unrealistically low. 9) Higher BCF values were reported, but this is the highest value for which lipid normalization could be applied. 10) In this study no lipid content was given, but for a lipid normalized value to fall below the trigger value of 5000 the lipid content needs to be 13%, which seems to be unrealistically high. 11) In this study no lipid content was given, but for a lipid normalized value to fall below the trigger value of 5000 the lipid content needs to be 28%, which seems to be unrealistically high. 12) In this study no lipid content was given, but for a lipid normalized value to fall below the trigger value of 5000 the lipid content needs to be 50%, which seems to be unrealistically high.

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The results from the present evaluation of BCF values are summarized in Table 2. This table shows that for most PAHs the same conclusions are reached for their bioaccumulative properties, i.e. naphthalene, acenaphthene, acenaphthylene and 9H-fluorene are considered not bioaccumulative, and chrysene, benzo[k]fluoranthene, benzo[ghi]perylene, and dibenz[a,h]anthracene are considered vB (based on invertebrates). Anthracene is still considered B for fish, but additional data show that it is vB in molluscs and crustaceans. For phenanthrene and fluoranthene, however, re-evaluation of data deemed these compounds B instead of vB when based on fish. Based on invertebrates (crustaceans for phenanthrene; mussels and crustaceans for fluoranthene) both compounds are considered vB. Similarly pyrene, benz[a]anthracene and benzo[a]pyrene do not accumulate in fish (due to biotransformation), but are very bioaccumulative at lower trophic levels (molluscs and crustaceans).

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References Ahrens MJ, Nieuwenhuis R and Hickey CW, 2002. Sensitivity of juvenile Macomona liliana (bivalvia) to

UV-photoactivated fluoranthene toxicity. Environ. Toxicol. 17: 567-577. Anderson JW, Neff JM, Cox BA, Tatem HE and Hightower GM, 1974. The effects of oil on estuarine

animals: toxicity, uptake and depuration, respiration. In: Vernberg FJ and Vernberg WB, eds. Pollution and Physiology of Marine Organisms. Academic Press, New York, NY, USA, pp. 367-379.

Ankley GT, Erickson RJ, Sheedy BR, Kosian PA, Mattson VR and Cox JS, 1997. Evaluation of models for predicting the phototoxic potency of polycyclic aromatic hydrocarbons. Aquat. Toxicol. 37: 37-50.

Arnot JA, Mackay D, Parkerton TF and Bonnell M, 2008. A database of fish biotransformation rates for organic chemicals. Environ. Toxicol. Chem. 27: 2263-2270.

Barrows ME, Petrocelli SR, Macek KJ and Carroll JJ, 1980. Bioconcentration and elimination of selected water pollutants by bluegill sunfish Lepomis macrochirus. In: Hague R, ed. Dynamic Exposure Hazard Assessment of Toxic Chemicals. Ann Arbor Science Publishers, Ann Arbor, Michigan, USA, pp. 379-392.

Baussant T, Sanni S, Jonsson G, Skadsheim A and Børseth JF, 2001a. Bioaccumulation of polycyclic aromatic compounds: 1. Bioconcentration in two marine species and in semipermeable membrane devices during chronic exposure to dispersed crude oil. Environ. Toxicol. Chem. 20: 1175-1184.

Baussant T, Sanni S, Skadsheim A, Jonsson G, Børseth JF and Gaudebert B, 2001b. Bioaccumulation of polycyclic aromatic compounds: 2. Modeling bioaccumulation in marine organisms chronically exposed to dispersed oil. Environ. Toxicol. Chem. 20: 1185-1195.

Bayona JM, Fernandez P, Porte C, Tolosa I, Valls M and Albaiges J, 1991. Partitioning of urban wastewater organic microcontaminants among coastal compartments. Chemosphere 23: 313-326.

Black MC, Burton W, McCarthy JF, Peterson MJ and Southworth GR, 1993. Bioaccumulation studies. In: Hinzman RL, ed. Second Report on the Oak Ridge Y-12 Plant Biological Monitoring and Abatement Program for East Fork Poplar Creek. Publication Nr 3859. Oak Ridge National Laboratory, Environmental Sciences Division, Oak Ridge, TN, USA, pp. 109-172.

Boese BL, Ozretich RJ, Lamberson JO, Swartz RC, Cole FA, Pelletier J and Jones J, 1999. Toxicity and phototoxicity of mixtures of highly lipophilic PAH compounds in marine sediment: Can the ΣPAH model be extrapolated? Arch. Environ. Con. Tox. 36: 270-280.

Bruner KA, Fisher SW and Landrum PF, 1994. The role of the zebra mussel, Dreissena polymorpha, in contaminant cycling: I. The effect of body size and lipid content on the bioconcentration of PCBs and PAHs. J. Great Lakes Res. 20: 725-734.

Cailleaud K, Budzinski H, Le Menach K, Souissi S and Forget-Leray J, 2009. Uptake and elimination of hydrophobic organic contaminants in estuarine copepods: An experimental study. Environ. Toxicol. Chem. 28: 239-246.

Carls MG and Rice SD, 1988. Sensitivity differences between eggs and larvae of walleye pollock (Theragra chalcogramma) to hydrocarbons. Mar. Environ. Res. 26: 285-297.

Carlson RM, Oyler AR, Gerhart EH, Caple R, Welch KJ, Kopperman HL, Bodenner D and Swanson D, 1979. Implications to the aquatic environment of polynuclear aromatic hydrocarbons liberated from Northern Great Plains coal. US EPA report EPA-600/3-79-093, U.S. Environmental Protection Agency (US EPA), Duluth, MN.

Casserly DM, Davis EM, Downs TD and Guthrie RK, 1983. Sorption of organics by Selenastrum capricornutum. Wat. Res. 17: 1591-1594.

Cheikyula JO, Koyama J and Uno S, 2008. Comparative study of bioconcentration and EROD activity induction in the Japanese flounder, red sea bream, and Java medaka exposed to polycyclic aromatic hydrocarbons. Environ. Toxicol. 23: 354-362.

Chen S, Ke R, Zha J, Wang Z and Khan SU, 2008. Influence of humic acid on bioavailability and toxicity of benzo[k]fluoranthene to Japanese medaka. Environ. Sci. Technol. 42: 9431-9436.

Cho EA, Bailer AJ and Oris JT, 2003. Effect of methyl tert-butyl ether on the bioconcentration and photoinduced toxicity of fluoranthene in fathead minnow larvae (Pimephales promelas). Environ. Sci. Technol. 37: 1306-1310.

RIVM report 601779002 29

Page 31: RIVM report 601779002 Bioaccumulation of polycyclic ... · The present report gives an evaluation of reported BCF values for polycyclic aromatic hydrocarbons (PAHs) in aquatic organisms.

Clements WH, Oris JT and Wissing TE, 1994. Accumulation and food chain transfer of fluoranthene and benzo[a]pyrene in Chironomus riparius and Lepomis macrochirus. Arch. Environ. Con. Tox. 26: 261-266.

Correa M and Coler R, 1983. Enhanced oxygen uptake rates in dragonfly nymphs (Somatochlora cingulata) as an indication of stress from naphthalene. Bull. Environ. Contam. Toxicol. 30: 269-276.

Correa M and Venables BJ, 1985. Bioconcentration of naphthalene in tissues of the white mullet (Mugil curema). Environ. Toxicol. Chem. 4: 227-231.

Couch JA, Courtney LA, Winstead JT and Foss SS, 1979. American oyster (Crassostrea virginica) as an indicator of carcinogens in the aquatic environment. In: Animals as Monitors of Environmental Pollutants. National Academy of Sciences, Washington, DC, USA, pp. 65-84.

De Maagd PG-J, 1996. Polycyclic aromatic hydrocarbons: fate and effects in aquatic environment. Ph.D. thesis. Utrecht University, Utrecht, The Netherlands.

De Maagd PG-J, de Poorte J, Opperhuizen A and Sijm DTHM, 1998. No influence after various exposure times on the biotransformation rate constants of benzo(a)anthracene in fathead minnow (Pimephales promelas). Aquat. Toxicol. 40: 157-169.

De Voogt P, van Hattum B, Leonards P, Klamer JC and Govers H, 1991. Bioconcentration of polycyclic heteroaromatic hydrocarbons in the guppy (Poecilia reticulata). Aquat. Toxicol. 20: 169-194.

DiMichele L and Taylor MH, 1978. Histopathological and physiological responses of Fundulus heteroclitus to naphthalene exposure. J. Fish. Res. Board Can. 35: 1060-1066.

Djomo JE, Garrigues P and Narbonne JF, 1996. Uptake and depuration of polycyclic aromatic hydrocarbons from sediment by the zebrafish (Brachydanio rerio). Environ. Toxicol. Chem. 15: 1177-1181.

Dunn BP and Stich HF, 1976. Release of the carcinogen benzo(a)pyrene from environmentally contaminated mussels. Bull. Environ. Contam. Toxicol. 15: 398-401.

Duxbury CL, Dixon DG and Greenberg BM, 1997. Effects of simulated solar radiation on the bioaccumulation of polycyclic aromatic hydrocarbons by the duckweed Lemna gibba. Environ. Toxicol. Chem. 16: 1739-1748.

Eastmond DA, Booth GM and Lee ML, 1984. Toxicity, accumulation, and elimination of polycyclic aromatic sulfur heterocycles in Daphnia magna. Arch. Environ. Con. Tox. 13: 105-111.

ECHA, 2008. Guidance on information requirements and chemical safety assessment, Chapter R.11: PBT Assessment. Guidance for the implementation of REACH. European Chemicals Agency (ECHA), Helsinki, Finland.

EMBSI, 2001. Fish, dietary bioaccumulation test, study no. 100047AB. Report 01MRL61, ExxonMobil Biomedical Sciences Inc. (EMBSI), Annandale, NJ, USA.

EMBSI, 2005. Fish, dietary bioaccumulation test, study no. 100047P. Report 05MRL127, ExxonMobil Biomedical Sciences Inc. (EMBSI), Annandale, NJ, USA.

EMBSI, 2006. Fish, dietary bioaccumulation test, study no. 0681647. Report 06EMBSI506, ExxonMobil Biomedical Sciences Inc. (EMBSI), Annandale, NJ, USA.

EMBSI, 2007a. Fish, dietary bioaccumulation study, study no. 0711047. ExxonMobil Biomedical Sciences Inc. (EMBSI), Annandale, NJ, USA.

EMBSI, 2007b. Fish, dietary bioaccumulation study, study no. 0796347C. ExxonMobil Biomedical Sciences Inc. (EMBSI), Annandale, NJ, USA.

EMBSI, 2007c. Fish, dietary bioaccumulation study, study no. 0796347T. ExxonMobil Biomedical Sciences Inc. (EMBSI), Annandale, NJ, USA.

EMBSI, 2008a. Fish, dietary bioaccumulation study, study no. 0818447. ExxonMobil Biomedical Sciences Inc. (EMBSI), Annandale, NJ, USA.

EMBSI, 2008b. Fish, dietary bioaccumulation study, study no. 0821047. ExxonMobil Biomedical Sciences Inc. (EMBSI), Annandale, NJ, USA.

EMBSI, 2009. Fish, aqueous bioaccumulation study, study no. 0829644. ExxonMobil Biomedical Sciences Inc. (EMBSI), Annandale, NJ, USA.

EU, 1993. Council Regulation (EEC) No 793/93 of 23 March 1993 on the evaluation and control of the risks of existing substances. O. J. L 84: 1-75.

EU, 2007. Corrigendum to Regulation (EC) No 1907/2006 of the European Parliament and of the Council of 18 December 2006 concerning the Registration, Evaluation, Authorisation and Restriction of Chemicals (REACH), establishing a European Chemicals Agency, amending Directive 1999/45/EC and repealing Council Regulation (EEC) No 793/93 and Commission Regulation (EC) No 1488/94

30 RIVM report 601779002

Page 32: RIVM report 601779002 Bioaccumulation of polycyclic ... · The present report gives an evaluation of reported BCF values for polycyclic aromatic hydrocarbons (PAHs) in aquatic organisms.

as well as Council Directive 76/769/EEC and Commission Directives 91/155/EEC, 93/67/EEC, 93/105/EC and 2000/21/EC. O. J. L 136: 3-280.

Evans MS and Landrum PF, 1989. Toxicokinetics of DDE, benzo(a)pyrene, and 2,4,5,2',4',5'-hexachlorobiphenyl in Pontoporeia hoyi and Mysis relicta. J. Great Lakes Res. 15: 589-600.

Fan CW and Reinfelder JR, 2003. Phenanthrene accumulation kinetics in marine diatoms. Environ. Sci. Technol. 37: 3405-3412.

Finger SE, Little EF, Henry MG, Fairchild JF and Boyle TP, 1985. Comparison of laboratory and field assessment of fluorene - Part I: Effects of fluorene on the survival, growth, reproduction, and behavior of aquatic organisms in laboratory tests. In: Boyle TP, ed. Validation and Predictability of Laboratory Methods for Assessing the Fate and Effects of Contaminants in Aquatic Ecosystems. American Society for Testing and Materials, Philadelphia, PA, USA

Frank AP, Landrum PF and Eadie BJ, 1986. Polycyclic aromatic hydrocarbon rates of uptake, depuration, and biotransformation by Lake Michigan Stylodrilus heringianus. Chemosphere 15: 317-330.

Freitag D, Ballhorn L, Geyer H and Korte F, 1985. Environmental hazard profile of organic chemicals. An experimental method for the assessment of the behaviour of organic chemicals in the ecosphere by means of simple laboratory tests with 14C labelled chemicals. Chemosphere 14: 1589-1616.

Freitag D, Geyer H and Kraus A, 1982. Ecotoxicological profile analysis. VII. Screening chemicals for their environmental behavior by comparative evaluation. Ecotox. Environ. Saf. 6: 60-81.

Gerould S, Landrum P and Giesy JP, 1983. Anthracene bioconcentration and biotransformation in chironomids: Effects of temperature and concentration. Environ. Pollut. Ser. A 30: 175-188.

Geyer H, Politzki G and Freitag D, 1984. Prediction of ecotoxicological behaviour of chemicals: Relationship between n-octanol/water partition coefficient and bioaccumulation of organic chemicals by alga Chlorella. Chemosphere 13: 269-284.

Gharrett JA and Rice SD, 1987. Influence of simulated tidal cycles on aromatic hydrocarbon uptake and elimination by the shore crab Hemigrapsus nudus. Mar. Biol. 95: 365-370.

Gobas FAPC, de Wolf W, Burkhard LP, Verbruggen E and Plotzke K, 2009. Revisiting bioaccumulation criteria for POPs and PBT assessments. Integr. Environ. Assess. Manag. 5: 624-637.

Gossiaux DC, Landrum PF and Fisher SW, 1996. Effect of temperature on the accumulation kinetics of PAHs and PCBs in the zebra mussel, Dreissena polymorpha. J. Great Lakes Res. 22: 379-388.

Granier LK, Lafrance P and Campbell PGC, 1999. An experimental design to probe the interactions of dissolved organic matter and xenobiotics: Bioavailability of pyrene and 2,2',5,5'-tetrachlorobiphenyl to Daphnia magna. Chemosphere 38: 335-350.

Haitzer M, Abbt-Braun G, Traunspurger W and Steinberg CEW, 1999a. Effects of humic substances on the bioconcentration of polycyclic aromatic hydrocarbons: Correlations with spectroscopic and chemical properties of humic substances. Environ. Toxicol. Chem. 18: 2782-2788.

Haitzer M, Höss S, Traunspurger W and Steinberg C, 1999b. Relationship between concentration of dissolved organic matter (DOM) and the effect of DOM on the bioconcentration of benzo[a]pyrene. Aquat. Toxicol. 45: 147-158.

Hall AT, 1993. Reproductive and behavioral toxicity of anthracene in the fathead minnow (Pimephales promelas). PhD Thesis. Miami University, Oxford, OH, USA.

Hall AT and Oris JT, 1991. Anthracene reduces reproductive potential and is maternally transferred during long-term exposure in fathead minnows. Aquat. Toxicol. 19: 249-264.

Halling-Sørensen B, Nyholm N, Kusk KO and Jacobsson E, 2000. Influence of nitrogen status on the bioconcentration of hydrophobic organic compounds to Selenastrum capricornutum. Ecotox. Environ. Saf. 45: 33-42.

Herbes SE, 1976. Transport and bioaccumulation of polycyclic aromatic hydrocarbons (PAH) in aquatic systems. In: Coal Technology Program Quarterly Progress Report for the Period Ending December 31, 1975. Oak Ridge National Laboratory, Oak Ridge, TN, USA, pp. 65-71.

Herbes SE and Risi GF, 1978. Metabolic alteration and excretion of anthracene by Daphnia pulex. Bull. Environ. Contam. Toxicol. 19: 147-155.

Jimenez BD, Cirmo CP and McCarthy JF, 1987. Effects of feeding and temperature on uptake, elimination and metabolism of benzo[a]pyrene in the bluegill sunfish (Lepomis macrochirus). Aquat. Toxicol. 10: 41-57.

Johnsen S, Kukkonen J and Grande M, 1989. Influence of natural aquatic humic substances on the bioavailability of benzo(a)pyrene to Atlantic Salmon. Sci. Total Environ. 81-82: 691-702.

RIVM report 601779002 31

Page 33: RIVM report 601779002 Bioaccumulation of polycyclic ... · The present report gives an evaluation of reported BCF values for polycyclic aromatic hydrocarbons (PAHs) in aquatic organisms.

Jonker MTO and Van der Heijden SA, 2007. Bioconcentration factor hydrophobicity cutoff: An artificial phenomenon reconstructed. Environ. Sci. Technol. 41: 7363-7369.

Jonsson G, Bechmann RK, Bamber SD and Baussant T, 2004. Bioconcentration, biotransformation, and elimination of polycyclic aromatic hydrocarbons in sheepshead minnows (Cyprinodon variegatus) exposed to contaminated seawater. Environ. Toxicol. Chem. 23: 1538-1548.

Kane Driscoll S, Landrum PF and Tigue E, 1997. Accumulation and toxicokinetics of fluoranthene in water-only exposures with freshwater amphipods. Environ. Toxicol. Chem. 16: 754-761.

Kira S, Nogami Y, Taketa K and Hayatsu H, 1996. Comparison of techniques for monitoring water-borne polycyclic mutagens: Efficiency of blue rayon, sep-pak C18, and a biota, Corbicula, in concentrating benzo(a)pyrene in a model water system. Bull. Environ. Contam. Toxicol. 57: 278-283.

Klimisch HJ, Andreae M and Tillmann U, 1997. A systematic approach for evaluating the quality of experimental toxicological and ecotoxicological data. Regul. Toxicol. Pharmacol. 25: 1-5.

Kuhnhold WW and Busch F, 1978. On the uptake of three different types of hydrocarbons by salmon eggs (Salmo salar L.). Meeresforschung 26: 50-59.

Kukkonen J, McCarthy JF and Oikari A, 1990. Effects of XAD-8 fractions of dissolved organic carbon on the sorption and bioavailability of organic micropollutants. Arch. Environ. Con. Tox. 19: 551-557.

Lampi M and Parkerton T, 2008. Bioaccumulation Assessment of PAHs - Draft. ExxonMobil Biomedical Sciences, Inc.

Lampi M and Parkerton T, 2009. Bioaccumulation Assessment of PAHs - Draft. ExxonMobil Biomedical Sciences, Inc. (EMBSI).

Landrum PF, 1982. Uptake, depuration and biotransformation of anthracene by the scud Pontoporeia hoyi. Chemosphere 11: 1049-1057.

Landrum PF, 1988. Toxicokinetics of organic xenobiotics in the amphipod, Pontoporeia hoyi: Role of physiological and environmental variables. Aquat. Toxicol. 12: 245-271.

Landrum PF, Lotufo GR, Gossiaux DC, Gedeon ML and Lee JH, 2003. Bioaccumulation and critical body residue of PAHs in the amphipod, Diporeia spp.: Additional evidence to support toxicity additivity for PAH mixtures. Chemosphere 51: 481-489.

Landrum PF and Poore R, 1988. Toxicokinetics of selected xenobiotics in Hexagenia limbata. J. Great Lakes Res. 14: 427-437.

Landrum PF and Scavia D, 1983. Influence of sediment on anthracene uptake, depuration, and biotransformation by the amphipod Hyalella azteca. Can. J. Fish. Aquat. Sci. 40: 298-305.

Laurén DJ and Rice S, 1985. Significance of active and passive depuration in the clearance of naphthalene from the tissues of Hemigrapsus nudus (Crustacea: Decapoda). Mar. Biol. 88: 135-142.

Lee JH, Landrum PF and Koh CH, 2002. Toxicokinetics and time-dependent PAH toxicity in the amphipod Hyalella azteca. Environ. Sci. Technol. 36: 3124-3130.

Lee RF, Sauerheber R and Dobbs GH, 1972. Uptake, metabolism and discharge of polycyclic aromatic hydrocarbons by marine fish. Mar. Biol. 17: 201-208.

Leversee GJ, Giesy JP, Landrum PF, Bartell S, Gerould S, Bruno M, Spacie A, Bonling J, Haddock J and Fannin T, 1981. Disposition of benzo(a)pyrene in aquatic system components: periphyton, chironomids, daphnia, fish. In: Cooke M and Dennis AJ, eds. Analysis and Biological Fate: Polynuclear Aromatic HydroCarbons. Batelle Press, Columbus, OH, USA, pp. 357-366.

Leversee GJ, Giesy JP, Landrum PF, Gerould S, Bowling JW, Fannin TE, Haddock JD and Bartell SM, 1982. Kinetics and biotransformation of benzo(a)pyrene in Chironomus riparius. Arch. Environ. Con. Tox. 11: 25-31.

Leversee GJ, Landrum PF, Giesy JP and Fannin T, 1983. Humic acids reduce bioaccumulation of some polycyclic aromatic hydrocarbons. Can. J. Fish. Aquat. Sci. 40: s63–s69.

Levine SL, Czosnyka H and Oris JT, 1997. Effect of the fungicide clotrimazole on the bioconcentration of benzo[a]pyrene in Gizzard shad (Dorosoma cepedianum): In vivo and in vitro inhibition of cytochrome P4501A activity. Environ. Toxicol. Chem. 16: 306-311.

Linder G, 1982. Anthracene bioconcentration in rainbow trout in single-compound and complex chemical mixture exposures. PhD Thesis. University of Wyoming, Laramie, WY, USA.

Linder G and Bergman HL, 1984. Periodic depuration of anthracene metabolites by rainbow trout. T. Am. Fish. Soc. 113: 513-520.

32 RIVM report 601779002

Page 34: RIVM report 601779002 Bioaccumulation of polycyclic ... · The present report gives an evaluation of reported BCF values for polycyclic aromatic hydrocarbons (PAHs) in aquatic organisms.

Linder G, Bergman HL and Meyer JS, 1985. Anthracene bioconcentration in rainbow trout during single-compound and complex-mixture exposures. Environ. Toxicol. Chem. 4: 549-558.

Liu ZT, Kong ZM, Zhou F and Wang LS, 1996. Bioconcentration and toxicity effect on lipid content of aquatic organisms. Bull. Environ. Contam. Toxicol. 56: 135-142.

Lockhart WL, Metner DA, Billeck BN, Rawn GP and Muir DCG, 1983. Bioaccumulation of some forestry pesticides in fish and aquatic plants. In: Chemical and Biological Controls in Forestry. ACS Symposium Series. 238. American Chemical Society, Washington, D.C., pp. 297-318.

Lu PY, Metcalf RL, Plummer N and Mandel D, 1977. The environmental fate of three carcinogens: Benzo-(α)-pyrene, benzidine, and vinyl chloride evaluated in laboratory model ecosystems. Arch. Environ. Con. Tox. 6: 129-142.

Mailhot H, 1987. Prediction of algal bioaccumulation and uptake rate of nine organic compounds by ten physicochemical properties. Environ. Sci. Technol. 21: 1009-1013.

McCarthy JF, 1983. Role of particulate organic matter in decreasing accumulation of polynuclear aromatic hydrocarbons by Daphnia magna. Arch. Environ. Con. Tox. 12: 559-568.

McCarthy JF and Jimenez BD, 1985. Reduction in bioavailability to bluegills of polycyclic aromatic hydrocarbons bound to dissolved humic material. Environ. Toxicol. Chem. 4: 511-521.

McCarthy JF, Jimenez BD and Barbee T, 1985. Effect of dissolved humic material on accumulation of polycyclic aromatic hydrocarbons: Structure-activity relationships. Aquat. Toxicol. 7: 15-24.

McLeese DW and Burridge LE, 1987. Comparative accumulation of PAHs in four marine invertebrates. In: Capuzzo JM and Kester DR, eds. Biological Processes and Wastes in the Ocean. Oceanic Processes in Marine Pollution. 1. Robert E Krieger, Malabar, FL, USA, pp. 109-118.

Melancon Jr MJ and Lech JJ, 1978. Distribution and elimination of naphthalene and 2-methylnaphthalene in rainbow trout during short- and long-term exposures. Arch. Environ. Con. Tox. 7: 207-220.

Monson PD, Call DJ, Cox DA, Liber K and Ankley GT, 1999. Photoinduced toxicity of fluoranthene to northern leopard frogs (Rana pipiens). Environ. Toxicol. Chem. 18: 308-312.

Moy FE and Walday M, 1997. Accumulation and depuration of organic micro-pollutants in marine hard bottom organisms. Mar. Pollut. Bull. 33: 56-63.

Murray AP, Richardson BJ and Gibbs CF, 1991. Bioconcentration factors for petroleum hydrocarbons, PAHs, LABs and biogenic hydrocarbons in the blue mussel. Mar. Pollut. Bull. 22: 595-603.

Neff JM and Anderson JW, 1975. Accumulation, release and distribution of benzo[a]pyrene-C14 in the clam Rangia cuncata. In: Proceedings of the Conference on Prevention and Control of Oil Pollution, March 25-27, 1975. American Petroleum Institute, Washington, DC, USA, pp. 469-471.

Neff JM, Anderson JW, Cox BA, Laughlin Jr. RB, Rossi SS and Tatem HE, 1976a. Effects of petroleum on survival, respiration and growth of marine animals. In: Sources, Effects and Sinks of Hydrocarbons in the Aquatic Environment. American Institute of Biological Sciences, Arlington, VA, USA, pp. 515-539.

Neff JM, Cox BA, Anderson JW and Dixit D, 1976b. Accumulation and release of petroleum derived aromatic hydrocarbons by four species of marine animals. Mar. Biol. 38: 279-289.

Netherlands, 2008. Coal Tar Pitch High Temperature. Documentation of the work done under the Existing Substance Regulation (EEC) No 793/93 and submitted to the European Chemicals Agency according to Article 136(3) of Regulation (EC) No 1907/2006. Annex XV Transitional Dossier, Rapporteur: the Netherlands. European Chemicals Agency, Helsinki, Finland.

Newsted JL and Giesy JP, 1987. Predictive models for photoinduced acute toxicity of polycyclic aromatic hydrocarbons to Daphnia magna, Strauss (Cladocera, Crustacea). Environ. Toxicol. Chem. 6: 445-461.

Nfon E, Cousins IT and Broman D, 2008. Biomagnification of organic pollutants in benthic and pelagic marine food chains from the Baltic Sea. Sci. Total Environ. 397: 190-204.

Niimi AJ and Dookhran GP, 1989. Dietary absorption efficiencies and elimination rates of polycyclic aromatic hydrocarbons (PAHs) in rainbow trout (Salmo gairdneri). Environ. Toxicol. Chem. 8: 719-722.

Niimi AJ and Palazzo V, 1986. Biological half-lives of eight polycyclic aromatic hydrocarbons (PAHs) in rainbow trout (Salmo gairdneri). Wat. Res. 20: 503-507.

OECD, 1996. OECD Guideline for Testing of Chemicals 305: Bioconcentration: Flow-through Fish Test. Organisation for Econonomic Co-operation and Development (OECD), Paris, France.

RIVM report 601779002 33

Page 35: RIVM report 601779002 Bioaccumulation of polycyclic ... · The present report gives an evaluation of reported BCF values for polycyclic aromatic hydrocarbons (PAHs) in aquatic organisms.

Ogata M, Fujisawa K, Ogino Y and Mano E, 1984. Partition coefficients as a measure of bioconcentration potential of crude oil compounds in fish and shellfish. Bull. Environ. Contam. Toxicol. 33: 561-567.

Oris JT, Hall AT and Tylka JD, 1990. Humic acids reduce the photo-induced toxicity of anthracene to fish and daphnia. Environ. Toxicol. Chem. 9: 575-583.

OSPAR. 1992. OSPAR Convention. http://www.ospar.org. Palmork KH and Solbakken JE, 1981. Distribution and elimination of [9-14C]phenanthrene in the horse

mussel (Modiola modiolus). Bull. Environ. Contam. Toxicol. 26: 196-201. Parkerton TF, Arnot JA, Weisbrod AV, Russom C, Hoke RA, Woodburn K, Traas T, Bonnell M, Burkhard

LP and Lampi MA, 2008. Guidance for evaluating in vivo fish bioaccumulation data. Integr. Environ. Assess. Manag. 4: 139-155.

Petersen GI and Kristensen P, 1998. Bioaccumulation of lipophilic substances in fish early life stages. Environ. Toxicol. Chem. 17: 1385-1395.

Rantamäki P, 1997. Release and retention of selected polycyclic aromatic hydrocarbons (PAH) and their methylated derivatives by the common mussel (Mytilus edulis) in the brackish water of the Baltic Sea. Chemosphere 35: 487-502.

Richardson BJ, Tse ES-C, De Luca-Abbott SB, Martin M and Lam PKS, 2005. Uptake and depuration of PAHs and chlorinated pesticides by semi-permeable membrane devices (SPMDs) and green-lipped mussels (Perna viridis). Mar. Pollut. Bull. 51: 975-993.

RIITI, 1977. Anthracene. The Official Bulletin of the Ministry of International Trade and Industry. Research Insititute of International Trade and Industry (RIITI), Tokyo, Japan.

RIITI, 1979. Naphthalene. The Official Bulletin of the Ministry of International Trade and Industry. Research Insititute of International Trade and Industry (RIITI), Tokyo, Japan.

RIITI, 1990a. Acenaphthene. The Official Bulletin of the Ministry of International Trade and Industry. Research Insititute of International Trade and Industry (RIITI), Tokyo, Japan.

RIITI, 1990b. Acenaphthylene. The Official Bulletin of the Ministry of International Trade and Industry. Research Insititute of International Trade and Industry (RIITI), Tokyo, Japan.

RIITI, 1990c. Fluorene. The Official Bulletin of the Ministry of International Trade and Industry. Research Insititute of International Trade and Industry (RIITI), Tokyo, Japan.

Riley RT, Mix MC, Schaffer RL and Bunting DL, 1981. Uptake and accumulation of naphthalene by the oyster Ostrea edulis, in a flow-through system. Mar. Biol. 61: 267-276.

Roubal WT, Stranahan SI and Malins DC, 1978. The accumulation of low molecular weight aromatic hydrocarbons of crude oil by Coho salmon (Oncorhynchus kisutch) and starry flounder (Platichthys stellatus). Arch. Environ. Con. Tox. 7: 237-244.

Schuler LJ, Landrum PF and Lydy MJ, 2004. Time-dependent toxicity of fluoranthene to freshwater invertebrates and the role of biotransformation on lethal body residues. Environ. Sci. Technol. 38: 6247-6255.

Seaton CL and Tjeerdema RS, 1996. Tissue disposition and biotransformation of naphthalene in striped bass (Morone saxatilis). Mar. Environ. Res. 42: 345-348.

Sheedy BR, Mattson VR, Cox JS, Kosian PA, Phipps GL and Ankley GT, 1998. Bioconcentration of polycyclic aromatic hydrocarbons by the freshwater oligochaete Lumbriculus variegatus. Chemosphere 36: 3061-3070.

Skarphéðinsdóttir H, Ericson G, Dalla Zuanna L and Gilek M, 2003. Tissue differences, dose-response relationship and persistence of DNA adducts in blue mussels (Mytilus edulis L.) exposed to benzo[a]pyrene. Aquat. Toxicol. 62: 165-177.

Southworth GR, Beauchamp JJ and Schmieder PK, 1978. Bioaccumulation potential of polycyclic aromatic hydrocarbons in Daphnia pulex. Wat. Res. 12: 973-977.

Spacie A, Landrum PF and Leversee GJ, 1983. Uptake, depuration, and biotransformation of anthracene and benzo[a]pyrene in bluegill sunfish. Ecotox. Environ. Saf. 7: 330-341.

Stockholm Convention. 2001. Stockholm Convention on Persistent Organic Pollutants (POPs). http://www.pops.int/.

Takeuchi I, Miyoshi N, Mizukawa K, Takada H, Ikemoto T, Omori K and Tsuchiya K, 2009. Biomagnification profiles of polycyclic aromatic hydrocarbons, alkylphenols and polychlorinated biphenyls in Tokyo Bay elucidated by δ13C and δ15N isotope ratios as guides to trophic web structure. Mar. Pollut. Bull. 58: 663-671.

34 RIVM report 601779002

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Tolls J, Haller M, Labee E, Verweij M and Sijm DTHM, 2000. Experimental determination of bioconcentration of the nonionic surfactant alcohol ethoxylate. Environ. Toxicol. Chem. 19: 646-653.

Trucco RG, Engelhardt FR and Stacey B, 1983. Toxicity, accumulation and clearance of aromatic hydrocarbons in Daphnia pulex. Environ. Pollut. Ser. A 31: 191-202.

US-EPA, 1976. Semi-Annual Report. April-September 1976. U.S. Environmental Protection Agency (US EPA), Gulf Breeze, FL, USA.

Van Hattum B and Cid Montañes JF, 1999. Toxicokinetics and bioconcentration of polycyclic aromatic hydrocarbons in freshwater isopods. Environ. Sci. Technol. 33: 2409-2417.

Veith GD, DeFoe DL and Bergstedt BV, 1979. Measuring and estimating the bioconcentration factor of chemicals in fish. J. Fish. Res. Board Can. 36: 1040-1048.

Veith GD, Macek KJ, Petrocelli SR and Carroll J, 1980. An evaluation of using partition coefficients and water solubility to estimate bioconcentration factors for organic chemicals in fish. In: Eaton JG, Parrish PR, and Hendricks AC, eds. Aquatic Toxicology. ASTM STP 707. American Society for Testing and Materials, Philadelphia, PA, USA, pp. 116-129.

Wan Y, Jin X, Hu J and Jin F, 2007. Trophic dilution of polycyclic aromatic hydrocarbons (PAHs) in a marine food web from Bohai Bay, North China. Environ. Sci. Technol. 41: 3109-3114.

Wang X and Wang WX, 2006. Bioaccumulation and transfer of benzo(a)pyrene in a simplified marine food chain. Mar. Ecol. Prog. Ser. 312: 101-111.

Weinstein JE, 2001. Characterization of the acute toxicity of photoactivated fluoranthene to glochidia of the freshwater mussel, Utterbackia imbecillis. Environ. Toxicol. Chem. 20: 412-419.

Weinstein JE, 2002. Photoperiod effects on the UV-induced toxicity of fluoranthene to freshwater mussel glochidia: Absence of repair during dark periods. Aquat. Toxicol. 59: 153-161.

Weinstein JE and Garner TR, 2008. Piperonyl butoxide enhances the bioconcentration and photoinduced toxicity of fluoranthene and benzo[a]pyrene to larvae of the grass shrimp (Palaemonetes pugio). Aquat. Toxicol. 87: 28-36.

Weinstein JE and Oris JT, 1999. Humic acids reduce the bioaccumulation and photoinduced toxicity of fluoranthene to fish. Environ. Toxicol. Chem. 18: 2087-2094.

Weinstein JE and Polk KD, 2001. Phototoxicity of anthracene and pyrene to glochidia of the freshwater mussel Utterbackia imbecillis. Environ. Toxicol. Chem. 20: 2021-2028.

Weinstein JE, Sanger DM and Holland AF, 2003. Bioaccumulation and toxicity of fluoranthene in the estuarine oligochaete Monopylephorus rubroniveus. Ecotox. Environ. Saf. 55: 278-286.

Weston DP, 1990. Hydrocarbon bioaccumulation from contaminated sediment by the deposit-feeding polychaete Abarenicola pacifica. Mar. Biol. 107: 159-169.

Widdows J, Moore SL, Clarke KR and Donkin P, 1983. Uptake, tissue distribution and elimination of [1-14C] naphthalene in the mussel Mytilus edulis. Mar. Biol. 76: 109-114.

Wilcoxen SE, Meier PG and Landrum PF, 2003. The toxicity of fluoranthene to Hyalella azteca in sediment and water-only exposures under varying light spectra. Ecotox. Environ. Saf. 54: 105-117.

Wildi E, Nagel R and Steinberg CEW, 1994. Effects of pH on the bioconcentration of pyrene in the larval midge, Chironomus riparius. Wat. Res. 28: 2553-2559.

Yakata N, Sudo Y and Tadokoro H, 2006. Influence of dispersants on bioconcentration factors of seven organic compounds with different lipophilicities and structures. Chemosphere 64: 1885-1891.

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Annex I Overview of BCF values from studies that were rated as not reliable (validity 3)

Species Exp. type a)

Test b)

Total BCF (ww) c)

Parent BCF (ww) d)

Type e)

Reliability remark f) Ref. g)

Naphthalene Pisces Brachydanio rerio (larvae)

SR UD 1778 – Equi. Value based on dry weight [47]

Brachydanio rerio (eggs)

SR UD 1820 – Equi. Value based on dry weight [47]

Cyprinodon variegatus

S UD nr nr – Short exposure to oil; concentra-tions only in graphs; steady state unlikely

[1]

Leuciscus idus melanotus

S U – 30 Equi. 3-day static exposure, no aeration

[17

Morone saxatilis FT1) U – 245.5 Equi. Exposure less than 96h [48] FT U – 283.7 Equi. Exposure less than 96h [48]Oncorhynchus mykiss2)

S U 71.5, 4153) – Equi. Static exposure, biotransforma-tion reported, BCF in bile

[40]

FT UD 13000 – Equi. Biotransformation reported, BCF in bile

[40]

FT U 25, 25, 1754)

– Equi. Biotransformation reported, BCF in different tissues

[40]

Pimephales promelas

S U – 302 Equi. No constant exposure, exposure less than 96h

[12]

Theragra chalcogramma (eggs)

S UD – 6.1 Equi. Short, static exposure; steady state unlikely

[5]

Theragra chalcogramma (larvae)

S UD – 51.3 Equi. Short, static exposure; steady state unlikely

[5]

Mollusca Rangia cuneata NR UD 9.30 6.1 Equi. No steady state [44]

Crustacea Daphnia magna S U – 57 – 745) Equi. Static exposure, only nominal

exposure concentration reported [30]

S U – 19 Kin. Short, static exposure; constant exposure unlikely

[38]

Hemigrapsus nudus S UD – 1270 Kin. BCF calculated based on con-centrations at beginning and end of depuration phase and nominal water concentrations

[27]

Insecta Somatochlora cingulata

S U – 24.9 – 15486)

Equi. Static exposure, no monitoring of water concentrations

[10]

Algae Chlorella fusca S U – 130 Equi. Static exposure, steady state

unlikely [18]

Selenastrum capricornutum

S U – 6965 Equi. Static exposure, steady state unlikely

[6]

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Species Exp. type a)

Test b)

Total BCF (ww) c)

Parent BCF (ww) d)

Type e)

Reliability remark f) Ref. g)

9H-Fluorene Pisces Poecilia reticulata S UD – 2230 Equi Short, static exposure [13]Oncorhynchus mykiss2) (larvae)

S UD 422, 512

– Kin.Equi.

Short, static exposure; decrease in exposure concentration

[34]

Scophthalmus maximus

FT UD – 33100 Equi Exposed to oil, PAH concen-tration > water solubility; BCF based on lipid weight

[2]

FT UD – 1451 Kin. Exposed to oil, PAH concen-tration > water solubility; BCF based on lipid weight

[3]

Oligochaeta Lumbriculus variegatus

SR U – 405, 5003) Equi. Exposure too short to reach steady state

[49]

Magnoliophyta Lemna minor NR UD 88,

105 nr Kin.

Equi.Based on total radioactivity of initial concentration

[34]

Anthracene Pisces Brachydanio rerio S UD 9500 – Kin. Sediment exposure, less than

96h; parent compound not distinguished

[14]

Carassius auratus NR U – 162 Equi. Exposure concentration and test system unknown

[45]

Lepomis macrochirus

S U – 675 Equi. Juveniles exposed for 4h only [51]

Leuciscus idus melanotus

S U – 910 Equi. 3-day static exposure, no aeration, no food

[16; 17]

Oncorhynchus mykiss2)

S UD – 190, 270 Equi. Decreasing exposure concen-tration, no steady state

[32]

SR UD – 5400 Equi. Exposure concentration above water solubility; exposure to a mixture

[33]

SR UD – 9100 Equi. Exposure concentration above water solubility

[33]

Pimephales promelas

S U – 6760 Kin. Decreasing exposure concen-tration, exposure less than 96h

[12]

Poecilia reticulata S UD – 7260 Equi. Static exposure, steady state unlikely

[13]

Scophthalmus maximus

FT UD – 17200 Equi. Animals exposed to oil; PAH concentration > water solubility; BCF based on lipid weight

[2]

Crustacea Asellus aquaticus S UD – 560 Equi. Short, static exposure; steady

state unlikely [52]

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Species Exp. type a)

Test b)

Total BCF (ww) c)

Parent BCF (ww) d)

Type e)

Reliability remark f) Ref. g)

Daphnia magna NR UD – 200 Equi. Exposure system and concen-tration unknown

[21]

S U – 319 – 6075) Equi. DOC present, only initial water concentration used; static expo-sure

[30]

S U – 230, 3705) Equi. Static exposure; also yeast present in system (as DOC), steady state unlikely

[39]

S U – 500 Equi. Static exposure; steady state unlikely

[39]

S U – 512 Kin. Static exposure; constant expo-sure unlikely

[38]

Hyalella azteca FT UD – 1419 Kin. Biotransformation reported, but not corrected for

[26]

FT UD 947 Kin. Exposure via sediment; author indicates this BCF to be mis-leading

[26]

FT UD 10985 9096 Equi. Exposure via sediment; author indicates this BCF to be mis-leading

[26]

Insecta Hexagenia sp. (nymph)

NR U 3500 Equi. Exposure system and concen-tration unknown; also yeast present in system (as DOC), steady state unlikely

[21]

Oligochaeta Lumbriculus variegatus

S U – 40700 Equi. Static exposure; sediment present; steady state unlikely

[24]

SR U – 1010, 14103)

Equi. Steady state unlikely; exposure concentration above water solubility

[49]

Algae Chlorella fusca S U – 7800 Equi. Static exposure; steady state

unlikely; exposure concentration above water solubility

[16]

S U – 7770 Equi. Static exposure; steady state unlikely; exposure concentration above water solubility

[18]

Selenastrum capricornutum

S U 7800 – Equi. Static exposure; steady state unlikely; little details on setup reported

[36]

Phenanthrene Pisces Brachydanio rerio S UD 11446 – Kin. Exposure via sediment for less

than 96h [14]

SR UD 7943 – 91203)

– Equi. BCF values based on dry weight; early life stages used

[47]

Clupea harengus SR UD 20893 – Equi. BCF values based on dry weight; early life stages used

[47]

Gadus morhua SR UD 10715 – Equi. BCF values based on dry weight; early life stages used

[47]

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Species Exp. type a)

Test b)

Total BCF (ww) c)

Parent BCF (ww) d)

Type e)

Reliability remark f) Ref. g)

Leuciscus idus melanotus

S U – 1760 Equi. No air or food was provided; exposure for 72h

[17]

Oryzias javanicus FT U – 150 Equi. Exposed to oversaturated PAH mixture

[7]

Pagrus major FT U – 180 Equi. Exposed to oversaturated PAH mixture

[7]

FT U – 173, 7372) Equi. Exposed to oversaturated PAH mixture ;BCF values in different tissues

[7]

Parlychthys olivaceus

FT U – 75 Equi. Exposed to oversaturated PAH mixture

[7]

FT U – 10, 1812) Equi. Exposed to oversaturated PAH mixture; BCF values in different tissues

[7]

Pimephales promelas

S U – 6760 Kin. Static exposure for less than 96h [12]

Scophthalmus maximus

FT UD – 10300 Equi. Exposure to oil, PAH concen-tration appears to be above water solubility

[2]

FT UD – 936 Kin. Exposure to oil, PAH concen-tration appears to be above water solubility

[3]

SR UD 11220 – Equi. BCF values based on dry weight; early life stages used

[47]

Mollusca Modiola modiolus S UD 3.1 – Equi. Low on experimental detail,

exposure concentration unclear. [46]

Rangia cuneata NR UD 240 32 Kin. Low on experimental detail, exposure type not reported; steady state not reached

[44]

Crustacea Asellus aquaticus S UD – 1300 Equi. Short, static exposure; steady

state unlikely [52]

Oligochaeta Lumbriculus variegatus

S U – 34700 Equi. Static exposure; sediment present; steady state unlikely

[24]

Algae Chlorella fusca S U – 1760 Equi. Short, static exposure; steady

state unlikely [18]

Selenastrum capricornutum

S U – 10620 Equi. Short, static exposure; steady state unlikely

[6]

S U 4.22 – 4.477)

– Equi. Static exposure; steady state unlikely; BCF value based on dry weight and total radioactivity

[20]

Thalassiosira pseudonana

S U 17 – Equi. Static exposure; steady state unlikely; BCF value based on dry weight and total radioactivity

[15]

Thalassiosira weissfloggii

S U 38.3 – Equi. Static exposure; steady state unlikely; BCF value based on dry weight and total radioactivity

[15]

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Species Exp. type a)

Test b)

Total BCF (ww) c)

Parent BCF (ww) d)

Type e)

Reliability remark f) Ref. g)

Fluoranthene Pisces Pimephales promelas

S U – 3388 Kin. Decreasing exposure concentration

[12]

Scophthalmus maximus

FT UD – >10000 Equi. Exposure to oil, PAH concen-tration above water solubility; BCF based on lipid weight

[2]

Mollusca Utterbackia imbecillis (glochidia)

SR U – 2147 Equi. BCF averaged for 5 different ex-posure concentrations; individual exposure concentrations uncer-tain

[56]

Crustacea Palaemonetes pugio (larvae)

SR U – 142 Equi. BCF averaged for different ex-posure concentrations; individual exposure concentrations uncer-tain

[54]

Oligochaeta Lumbriculus variegatus

S U – 27500 Equi. Static exposure; sediment present; steady state unlikely

[24]

FT U – 1510 – 30803)

Equi. Short exposure; steady state unlikely

[49]

Monopylephorus rubroniveus

SR U – 10893 Equi. BCF averaged for different ex-posure concentrations; individual exposure concentrations unce-tain

[55]

Pyrene Pisces Brachydanio rerio S UD 4333 – Kin. Exposure via sediment for less

than 96h [14]

SR UD 10000 – 549543)

– Equi. BCF values based on dry weight; early life stages used

[47]

Carassius auratus NR U – 457 Equi. Exposure concentration above water solubility

[45]

Clupea harengus SR UD 97724 – Equi. BCF values based on dry weight; early life stages used

[47]

Gadus morhua SR UD 60256 – Equi. BCF values based on dry weight; early life stages used

[47]

Oryzias javanicus FT U – 15 Equi. Exposed to oversaturated PAH mixture

[7]

Pagrus major FT U – 10 Equi. Exposed to oversaturated PAH mixture

[7]

FT U – 9, 572) Equi. Exposed to oversaturated PAH mixture ; BCF values in different tissues

[7]

Parlychthys olivaceus

FT U – 5 Equi. Exposed to oversaturated PAH mixture

[7]

FT U – 4, 522) Equi. Exposed to oversaturated PAH mixture ; BCF values in different tissues

[7]

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Species Exp. type a)

Test b)

Total BCF (ww) c)

Parent BCF (ww) d)

Type e)

Reliability remark f) Ref. g)

Poecilia reticulata S UD – 4810 Equi. Short, static exposure; steady state unlikely

[13]

Scophthalmus maximus

FT UD – <5000 Equi. Exposure to oil, PAH concen-tration above water solubility; BCF based on lipid weight

[2]

Mollusca Mytilus edulis FT UD – 334300 Equi. Exposure to oil, PAH concen-

tration above water solubility; BCF based on lipid weight

[2]

Crustacea Asellus aquaticus S UD – 2050 Equi. Short, static exposure; steady

state unlikely [52]

Oligochaeta Lumbriculus variegatus

S U – 380000 Equi. Static exposure; sediment present; steady state unlikely

[24]

SR U – 1480 – 23703)

Equi. Short exposure; steady state unlikely

[49]

Algae Selenastrum capricornutum

S U – 16760 Equi. Static exposure; steady state unlikely

[6]

Benz[a]anthracene Pisces Leuciscus idus melanotus

S U – 350 Equi. No food, no aeration; exposure concentration above water solubility

[17]

Scophthalmus maximus

FT UD – >10000 Equi. Exposure to oil, PAH concen-tration above water solubility; BCF based on lipid weight

[2]

Crustacea Daphnia magna S U – 2920 Kin. Static exposure; constant expo-

sure unlikely [38]

Oligochaeta Lumbriculus variegatus

S U – 3090000 Equi. Static exposure; sediment present; steady state unlikely

[24]

Algae Chlorella fusca S U – 3180 Equi. Static exposure; steady state

unlikely [17]

Chrysene Pisces Oryzias javanicus FT U – 10 Equi. Exposure concentration above

water solubility [7]

Pagrus major FT U – 15 Equi. Exposure concentration above water solubility

[7]

Scophthalmus maximus

FT UD – >10000 Equi. Exposure to oil, PAH concen-tration above water solubility; BCF based on lipid weight

[2]

FT UD – 54 Kin. Exposure to oil, PAH concen-tration above water solubility; BCF based on lipid weight

[3]

42 RIVM report 601779002

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Species Exp. type a)

Test b)

Total BCF (ww) c)

Parent BCF (ww) d)

Type e)

Reliability remark f) Ref. g)

Mollusca Rangia cuneata NR UD 31.56 8.2 Equi. Exposure type not reported;

steady state unlikely [44]

Crustacea Rhepoxynius abronius

SD U – 1141 Equi. Exposure via sediment; exposure concentration above water solu-bility

[4]

Oligochaeta Lumbriculus variegatus

S U – 3020000 Equi. Static exposure; sediment present; steady state unlikely

[24]

Benzo[a]pyrene Pisces Brachydanio rerio S UD 3600 – Kin. Exposure via sediment for less

than 96h [14]

SR UD 20893 – 3311313)

– Equi. BCF values based on dry weight; early life stages used

[47]

Dorosoma cepedianum

FT U – 3.2, 3.7 Equi. Short exposure; steady state unlikely

[31]

Gambusia affinis D U – 30 – 1403) Equi. Exposure in model ecosystem; exposure concentration appears to be above water solubility

[35]

Gillichthys mirabilis S U 20 – 74003,4)

Equi. Based on total radioactivity; based on several organs; short exposure concentration, steady state unlikely

[28]

Lepomis macrochirus

S U – 490 Equi. Very short static exposure; steady state unlikely

[51]

FT UD – 3208 Kin. Not fed; short exposure [22] FT UD – 225 Kin. Humic material present; short

exposure [37]

FT UD – 301 Equi. Humic material present; short exposure; steady state unlikely

[37]

Leuciscus idus melanotus

S U – 480 Equi. Short, static exposure; steady state unlikely

[17]

Oryzias javanicus FT U – 5 Equi. Exposed to oversaturated PAH mixture

[7]

Salmo salar FT UD 1160 – 23101)

– Kin. Short exposure; uncertain expo-sure concentration; based on total radioactivity

[23]

Mollusca Corbicula japonica FT U – 4 – 416) Equi. Short exposure; no constant

exposure concentration [25]

Crassostrea virginica

FT U – 236 – 2446) Equi. Initial concentration above water solubility; steady state unlikely; BCF values based on dry weight

[11]

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Species Exp. type a)

Test b)

Total BCF (ww) c)

Parent BCF (ww) d)

Type e)

Reliability remark f) Ref. g)

Mytilus edulis FT UD 255 – Equi. Based on total radioactivity but metabolism reported; no steady state

[41]

SR U 6294 – 152783,6)

– Equi. BCF based on dry weight and nominal exposure concentra-tions; photolytic breakdown possible

[50]

FD U – 100000 Equi. Field collected animals; BCF based on dry weight; exposure unclear

[42]

FD U – 1400000 Equi. Field collected animals; BCF based on lipid weight; exposure unclear

[42]

Physa spp. FT U – 4860 – 75203)

Equi. Exposed in model ecosystem; exposure concentrations appears to be above water solubility

[35]

Rangia cuneata S UD 187, 236 – Equi. No measured water concentra-tions reported; nominal exposure concentration > water solubility

[43]

NR UD 55.63 8.7 Equi. Short exposure to oil; no steady state; exposure type not reported

[44]

Crustacea Acartia erythraea S UD 5500000 24000 Kin. Short, static exposure; also

uptake via food [53]

Asellus aquaticus S UD – 32400 Equi. Short, static exposure; steady state unlikely

[52]

Daphnia magna S U – 838 – 27453,5)

Equi. Short, static exposure; DOC present; only initial exposure concentration used; steady state unlikely

[30]

S U – 1000 – 25005)

Equi. Short, static exposure; yeast present, resulting in dietary uptake as well; steady state unlikely

[39]

S U – 8250 Equi. Short, static exposure; biotrans-formation reported; no constant exposure; steady state unlikely

[39]

S U – 5771 Kin. Short, static exposure; constant exposure unlikely

[38]

Palaemonetes pugio (larvae)

SR U – 289 Equi. BCF averaged for different expo-sure concentrations; individual exposure concentrations uncertain

[54]

Insecta Chironomus riparius(4th instar larvae)

S U – 250 Equi. Exposure concentration reported in graphs only and above water solubility; sediment present

[9]

S UD – 200 Equi. Short, static exposure; reported BCF is average for several expo-sure concentrations; steady state unlikely

[29]

44 RIVM report 601779002

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Species Exp. type a)

Test b)

Total BCF (ww) c)

Parent BCF (ww) d)

Type e)

Reliability remark f) Ref. g)

Culex pipiens quinquefasciatus

D U – 2093 – 21203)

Equi. Exposed in model ecosystem; exposure concentration appears to be above water solubility

[35]

Oligochaeta Lumbriculus variegatus

S U – 18200000 Equi. Static exposure; sediment present; steady state unlikely

[24]

Nematoda Caenorhabiditis elegans

S U >25000 – Equi. Short exposure above water so-lubility; BCF reported in graphs only; steady state unlikely

[19]

Algae Chlorella fusca S U – 3300 Equi. Short, static exposure; steady

state unlikely [17]

Fucus vesiculosus FT UD 55.4 – Equi. Based on total radioactivity, but metabolism observed; steady state unlikely

[41]

Oedogonium cardiacum

D U – 3610, 41053)

Equi. Exposed in model ecosystem; exposure concentration appears to be above water solubility

[35]

Benzo[b]fluoranthene Mollusca Mytilus edulis FD U – 430000 Equi. Field collected animals; BCF

based on dry weight; exposure unclear

[42]

FD U – 2800000 Equi. Field collected animals; BCF based on lipid weight; exposure unclear

[42]

Oligochaeta Lumbriculus variegatus

S U – 13800000 Equi. Static exposure; sediment present; steady state unlikely

[24]

Benzo[k]fluoranthene Pisces Oryzias latipes nr U – 17 Equi. Only nominal exposure concen-

tration reported, concentration in fish only reported in graphs

[8]

Mollusca Mytilus edulis FD U – 300000 Equi. Field collected animals; BCF

based on dry weight; exposure unclear

[42]

FD U – 1700000 Equi. Field collected animals; BCF based on lipid weight; exposure unclear

[42]

Oligochaeta Lumbriculus variegatus

S U – 15100000 Equi. Static exposure; sediment present; steady state unlikely

[24]

Benzo[ghi]perylene Crustacea Asellus aquaticus S UD – 16000 Equi. Short, static exposure; steady

state unlikely [52]

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Species Exp. type a)

Test b)

Total BCF (ww) c)

Parent BCF (ww) d)

Type e)

Reliability remark f) Ref. g)

Oligochaeta Lumbriculus variegatus

S U – 33100000 Equi. Static exposure; sediment present; steady state unlikely

[24]

Dibenz[a,h]anthracene Pisces Leuciscus idus melanotus

S U – 10 Equi. Short, static exposure; steady state unlikely

[17]

Crustacea Daphnia magna S U – 666 – 9685) Equi. Short, static exposure; DOC pre-

sent; only initial exposure con-centration used; steady state unlikely

[30]

Oligochaeta Lumbriculus variegatus

S U – 20000000 Equi. Static exposure; sediment present; steady state unlikely

[24]

Algae Chlorella fusca S U – 2380 Equi. Short, static exposure; steady

state unlikely [17]

Indeno[1,2,3-cd]pyrene Oligochaeta Lumbriculus variegatus

S U – 39800000 Equi. Static exposure; sediment present; steady state unlikely

[24]

a) FD: organisms collected from the field; FT: flow-through system; S: static; SR: static renewal; NR: not reported. b) Test phases: U: uptake phase only; UD: both uptake and depuration phase. c) nr: not reported; –: only parent BCF available. d) nr: not reported; –: only total BCF available. e) Kin.: Kinetic BCF, i.e. k1/k2; Equi.: BCF at (assumed) equilibrium, i.e. Corganism/Cwater. f) Main reason(s) for rating the specific BCF value(s) as unreliable. f) References: [1] (Anderson et al., 1974); [2] (Baussant et al., 2001a); [3] (Baussant et al., 2001b); [4] (Boese et al., 1999); [5] (Carls and Rice, 1988); [6] (Casserly et al., 1983); [7] (Cheikyula et al., 2008); [8] (Chen et al., 2008); [9] (Clements et al., 1994); [10] (Correa and Coler, 1983); [11] (Couch et al., 1979); [12] (De Maagd, 1996); [13] (De Voogt et al., 1991); [14] (Djomo et al., 1996); [15] (Fan and Reinfelder, 2003); [16] (Freitag et al., 1982); [17] (Freitag et al., 1985); [18] (Geyer et al., 1984); [19] (Haitzer et al., 1999a; 1999b); [20] (Halling-Sørensen et al., 2000); [21] (Herbes, 1976); [22] (Jimenez et al., 1987); [23] (Johnsen et al., 1989); [24] (Jonker and Van der Heijden, 2007); [25] (Kira et al., 1996); [26] (Landrum and Scavia, 1983); [27] (Laurén and Rice, 1985); [28] (Lee et al., 1972); [29] (Leversee et al., 1982); [30] (Leversee et al., 1983); [31] (Levine et al., 1997); [32] (Linder and Bergman, 1984); [33] (Linder et al., 1985); [34] (Lockhart et al., 1983); [35] (Lu et al., 1977); [36] (Mailhot, 1987); [37] (McCarthy and Jimenez, 1985); [38] (McCarthy et al., 1985); [39] (McCarthy, 1983); [40] (Melancon Jr and Lech, 1978); [41] (Moy and Walday, 1997); [42] (Murray et al., 1991); [43] (Neff and Anderson, 1975); [44] (Neff et al., 1976a); [45] (Ogata et al., 1984); [46] (Palmork and Solbakken, 1981); [47] (Petersen and Kristensen, 1998); [48] (Seaton and Tjeerdema, 1996); [49] (Sheedy et al., 1998); [50] (Skarphéðinsdóttir et al., 2003); [51] (Spacie et al., 1983); [52] (Van Hattum and Cid Montañes, 1999); [53] (Wang and Wang, 2006); [54] (Weinstein and Garner, 2008); [55] (Weinstein et al., 2003); [56] (Weinstein, 2002) 1) Exposed in salt water (35 ‰). 2) Formerly known as Salmo gairdneri. 3) Values represent (a range of) BCF values from (a range of) different exposure concentrations. 4) Values represent BCF values for different tissues. 5) BCFs were determined at different DOC concentrations. 6) BCFs were determined at different exposure durations. 7) Values represent (a range of) BCF values for (a range of) different lipid contents.

46 RIVM report 601779002

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Annex II Overview of BCF values from studies for which validity was not assignable (validity 4)

Species Exp. type a)

Test b)

Total BCF (ww) c)

Parent BCF (ww) d)

Type e)

Reliability remark f) Ref. g)

Naphthalene Pisces Fundulus heteroclitus

S U 2.0, 2.21) – Equi. Based on total radioactivity [13]

S U 1.0 – 1051,2) – Equi. Based on total radioactivity; values for different organs

[13]

Gillichthys mirabilis S UD 263 – 37·106 1,2,3)

Kin. Based on total radioactivity; values for different organs

[25]

Mugil curema S U – 81 – 11582) Kin. Values for different organs [11]Oncorhynchus kisutch

FT U – 20 – 803) Equi. BCF based on dry weight [35]

Platichthys stellatus FT U – 150 – 11002,3)

Equi. BCF based on dry weight; values for different organs

[35]

FT UD – 100 – 7003) Equi. BCF based on dry weight [35]Salmo salar (eggs) S U – 18.5 –

82.51,3) Equi. Based on total radioactivity;

exposure of eggs [23]

Scophthalmus maximus

FT UD – 17800 Equi. Exposed to oil; BCF based on lipid weight

[3]

FT UD – 421 Kin. Exposed to oil [4] Mollusca Mytilus edulis FT UD – 266 Equi. Exposed to oil; BCF based on

lipid weight [3]

NR D nr nr – Only half-life reported [33] FT U – 48 Equi. Steady state reported, but no

exposure concentrations [43]

Ostrea edulis FT U – 24 – 592) Equi. Values for different organs [34]Rangia cuneata FT UD – 2.3 Equi. Exposed to oil [33]

Crustacea Daphnia magna S U 36.5 – Equi. Based on total radioactivity [6] S UD 50 – Equi. Based on total radioactivity [15]Daphnia pulex NR U 677, 23371) – Equi. Based on total radioactivity [37]Hemigrapsus nudus FT U 325 – Equi. Based on total radioactivity;

based on one organ [18]

Acenaphthene Pisces Lepomis macrochirus

S UD 387 nr Equi. Based on total radioactivity [2]

FT UD 387 nr Equi. Based on total radioactivity [38]Scophthalmus maximus

FT UD – 5500 Equi. Exposure to oil [3]

Mollusca Mytilus edulis FT UD – 1308 Equi. Exposed to oil [3]

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Species Exp. type a)

Test b)

Total BCF (ww) c)

Parent BCF (ww) d)

Type e)

Reliability remark f) Ref. g)

Acenaphthylene Pisces Oncorhynchus mykiss4)

D D – 128 Kin. Exposed via diet [30]

Scophthalmus maximus

FT UD – 53300 Equi. Exposure to oil [3]

Mollusca Mytilus edulis FT UD – 2892 Equi. Exposed to oil [3]

9H-Fluorene Pisces Lepomis macrochirus

FT U – 180 – 18001)

Equi. No details on exposure concentration

[16]

Oncorhynchus mykiss4)

D D – 589 Kin. Exposed via diet [31]

Poecilia reticulata SR U – 1050 Equi. No details on exposure concentration

[12]

Mollusca Mytilus edulis FT UD – 1018 Equi. Exposed to oil [3]

Crustacea Hyalella azteca SR UD 255 – 3151) – Kin. Based on total radioactivity [26]

Anthracene Pisces Oncorhynchus mykiss4)

D D – 773 Kin. Exposed via diet [31]

Pimephales promelas

SR U – 1016 Equi. Exposure concentration is unclear

[32]

Poecilia reticulata SR U – 4550 Equi. Exposure concentration uncertain, based on two fish only

[12]

Mollusca Utterbackia imbecillis (glochidia)

SR U – 247 – 4201) Equi. Value based on dry weight [41]

Crustacea Daphnia magna SR U – 2699 Equi. Exposure concentration unclear [32]Daphnia pulex S U 760 – Equi. Based on total radioactivity [21]Rhepoxynius abronius

SD U – 3267 – 267861)

Equi. Exposure via sediment [7]

Insecta Chironomus riparius(larvae)

FT U 47 – 19641) – Kin. Based on total radioactivity [17]

Polychaeta Capitella capitata FD nr – 23.6 Equi. Exposed in the field [5] Polychaete sp. FD nr – 6.6 Equi. Exposed in the field [5]

Phenanthrene Pisces Oncorhynchus mykiss4)

D D – 613 Kin. Exposed via diet [31]

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Species Exp. type a)

Test b)

Total BCF (ww) c)

Parent BCF (ww) d)

Type e)

Reliability remark f) Ref. g)

Mollusca Mytilus edulis FT UD – 2932 Equi. Exposed to oil [3] NR D nr nr – Only half-lives reported [33]

Crustacea Daphnia magna S UD 600 – Equi. Based on total radioactivity [15]Daphnia pulex NR U 1165 –

14241) – Equi. Based on total radioactivity [37]

Hyalella azteca SR UD 440 – 5041) – Kin. Based on total radioactivity [26]Polychaeta Capitella capitata FD nr – 30.7 Equi. Exposed in the field [5] Polychaete sp. FD nr – 5.7 Equi. Exposed in the field [5]

Fluoranthene Pisces Oncorhynchus mykiss4)

D D – 531 Kin. Exposed via diet [31]

Pimephales promelas

FT UD – 14836 Kin. Short exposure; BCF value maybe based on dry weight

[10]

SR U – 9054 Equi. BCF value based on dry weight [40]Mollusca Macomona liliana S UD 14 – Kin. Based on total radioactivity [1] Mytilus edulis FT UD – 2932 Equi. Exposed to oil [3] NR D nr nr – Only half-lives reported [33]

Crustacea Diporeia spp. SR UD 28095 –

567571) Kin. Based on nominal exposure

concentration [22]

Hyalella azteca SR UD 1932 – 23351)

Equi. Based on nominal exposure concentration

[22]

SR U 980 – 47411)

– Equi. Based on total radioactivity [44]

Rhepoxynius abronius

SD U – 18470 – 504841)

Equi. Exposure via sediment [7]

Polychaeta Capitella capitata FD nr – 12 Equi. Exposed in the field [5] Polychaete sp. FD nr – 5.7 Equi. Exposed in the field [5]

Pyrene Pisces Acanthogobius flavimanus

FD U – 61 Equi. Exposed in the field [36]

Poecilia reticulata SR U – 11300 Equi. Based on 2 fish only; little detail reported

[12]

Mollusca Mytilus edulis NR D nr nr Only half-lives reported [33]Utterbackia imbecillis (glochidia)

SR U – 830 – 12291)

Equi. Value based on dry weight [41]

Crustacea Daphnia magna S U 1400 – Equi. Based on total radioactivity [18]

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Species Exp. type a)

Test b)

Total BCF (ww) c)

Parent BCF (ww) d)

Type e)

Reliability remark f) Ref. g)

Hyalella azteca SR UD 2323 – 51651)

– Kin. Based on total radioactivity [26]

Polychaeta Capitella capitata FD nr – 13.3 Equi. Exposed in the field [5] Polychaete sp. FD nr – 5.2 Equi. Exposed in the field [5]

Nematoda Caenorhabiditis elegans

S U >11000 – Equi. Values only reported in graph only

[20]

Benz[a]anthracene Pisces Oncorhynchus mykiss4)

D D – 325 Kin. Exposed via diet [33]

Crustacea Daphnia pulex NR U 803 –

11061) – Equi. Based on total radioactivity [37]

Rhepoxynius abronius

SD U – 2832 – 254651)

Equi. Exposure via sediment [7]

Polychaeta Capitella capitata FD nr – 3.6 Equi. Exposed in the field [5] Polychaete sp. FD nr – 9.4 Equi. Exposed in the field [5]

Chrysene Crustacea Daphnia magna S UD 5500 – Equi. Based on total radioactivity [15]Eurytemora affinis FT U – 950 Equi. BCF value reported in graph only [8] Rhepoxynius abronius

SD U – 1560 – 210801)

Equi. Exposure via sediment [7]

Polychaeta Capitella capitata FD nr – 6.2 Equi. Exposed in the field [5] Polychaete sp. FD nr – 14.7 Equi. Exposed in the field [5]

Benzo[a]pyrene Pisces Gambusia affinis FT U – 22 Equi. Exposed in model ecosystem [28]Gillichthys mirabilis S U 158 –

57451) Kin. Based on total radioactivity;

based on several organs [25]

Lepomis macrochirus

S UD 4700 nr Kin. Based on total radioactivity [27]

Lutjanus argentimaculatus

S U 275000 nr Equi. Exposure in simplified marine food chain

[39]

Oligocottus maculosus

S U 70 – 2001) Equi. Based on total radioactivity; based on several organs

[25]

Oncorhynchus mykiss4)

D D – 261 Kin. Exposed via diet [31]

Oryzias javanicus FT U – 5 Equi. BCF value reported in graph only [9] Salmo salar (eggs) S U 8.2 –

70.71,3) – Equi. Based on total radioactivity [23]

Mollusca Mytilus edulis FD D nr nr – Only half-lives reported [14]Physa spp. FT U – 2177 Equi. Exposed in model ecosystem [28]

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Species Exp. type a)

Test b)

Total BCF (ww) c)

Parent BCF (ww) d)

Type e)

Reliability remark f) Ref. g)

FT U – 3056 Equi. Exposed to mixture in model ecosystem

[28]

Crustacea Acartia erythraea S UD 5500000 24000 Kin. Exposure in simplified marine

food chain [39]

Daphnia magna S U 5990 – Equi. Based on total radioactivity [6] S U 5990 – Equi. Based on total radioactivity [24]Daphnia pulex NR U 1259,

27201) – Equi. Based on total radioactivity [37]

Insecta Culex pipiens quinquefasciatus

FT U – 37 Equi. Exposed in model ecosystem [28]

FT U – 453 Equi. Exposed to mixture in model ecosystem

[28]

Polychaeta Aberenicola pacifica S U – 4700 –

110001) Equi. Exposed via sediment [42]

Capitella capitata FD nr – 0.7 Equi. Exposed in the field [5] Polychaete sp. FD nr – 13.8 Equi. Exposed in the field [5]

Benzo[b]fluoranthene Crustacea Eurytemora affinis FT U – 1300 Equi. Pooled value for benzo[k]fluoran-

thene and benzo[b]fluoranthene [8]

Rhepoxynius abronius

SD U – 1657 – 167721)

Equi. Exposure via sediment [7]

Polychaeta Capitella capitata FD nr – 1.7 Equi. Exposed in the field [5] Polychaete sp. FD nr – 9.1 Equi. Exposed in the field [5]

Benzo[k]fluoranthene Crustacea Eurytemora affinis FT U – 1300 Equi. Pooled value for benzo[k]fluoran-

thene and benzo[b]fluoranthene [8]

Polychaeta Capitella capitata FD nr – 1.8 Equi. Exposed in the field [5] Polychaete sp. FD nr – 14.1 Equi. Exposed in the field [5]

a FD: organisms collected from the field; FT: flow-through system; S: static; SR: static renewal; NR: not reported b) Test phases: U: uptake phase only; UD: both uptake and depuration phase. c) nr: not reported; –: only parent BCF available d) nr: not reported; –: only total BCF available. e) Kin.: Kinetic BCF, i.e. k1/k2; Equi.: BCF at (assumed) equilibrium, i.e. Corganism/Cwater. f) Main reason for rating the specific BCF value(s) not assignable. g) References: [1] (Ahrens et al., 2002); [2] (Barrows et al., 1980); [3] (Baussant et al., 2001a); [4] (Baussant et al., 2001b); [5] (Bayona et al., 1991); [6] (Black et al., 1993); [7] (Boese et al., 1999); [8] (Cailleaud et al., 2009); [9] (Cheikyula et al., 2008); [10] (Cho et al., 2003); [11] (Correa and Venables, 1985); [12] (De Voogt et al., 1991); [13] (DiMichele and Taylor, 1978); [14] (Dunn and Stich, 1976); [15] (Eastmond et al., 1984); [16] (Finger et al., 1985); [17] (Gerould et al., 1983); [18] (Gharrett and Rice, 1987); [18] (Granier et al., 1999); [20] (Haitzer et al., 1999a); [21] (Herbes and Risi, 1978); [22] (Kane Driscoll et al., 1997); [23] (Kuhnhold and Busch, 1978); [24] (Kukkonen et al., 1990); [25] (Lee et al., 1972); [26] (Lee et al., 2002); [27] (Leversee et al., 1981); [28] (Lu et al., 1977); [29] (Neff et al., 1976b); [30] (Niimi and Dookhran, 1989); [31] (Niimi and Palazzo, 1986); [32] (Oris et al., 1990); [33] (Rantamäki, 1997); [34] (Riley et al., 1981); [35] (Roubal et al., 1978); [36] (Takeuchi et al., 2009); [37] (Trucco et al., 1983); [38] (Veith et al., 1980); [39] (Wang and Wang, 2006); [40] (Weinstein and Oris, 1999); [41] (Weinstein and Polk, 2001); [42] (Weston, 1990); [43] (Widdows et al., 1983); [44] (Wilcoxen et al., 2003). 1) Values represent (a range of) BCF values from (a range of) different exposure concentrations. 2) Values represent BCF values for different tissues. 3) BCFs were determined at different exposure durations.4) Formerly known as Salmo gairdneri.

RIVM report 601779002 51

Page 53: RIVM report 601779002 Bioaccumulation of polycyclic ... · The present report gives an evaluation of reported BCF values for polycyclic aromatic hydrocarbons (PAHs) in aquatic organisms.

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