Common Implementation Strategy for the Water Framework Directive. Fluoranthene

Transcription

1 Common Implementation Strategy for the Water Framework Directive Environmental Quality Standards (EQS) Substance Data Sheet Priority Substance No. 15 Fluoranthene CAS-No Final version Brussels, 15 January 2005

2 Disclaimer This data sheet provides background information on the setting of the Environmental Quality Standard in accordance with Article 16 of the Water Framework Directive (2000/60/EC). The information was compiled, evaluated and used as outlined in the Manual [4] and has been discussed in a consultative process with the Expert Advisory Forum on Priority Substances and the Expert Group on Quality Standards. Furthermore, it has been peer-reviewed by the SCTEE [14]. The substance data sheet may, however, not necessarily represent the views of the European Commission. New upcoming information was considered and included up to the date of finalisation of this data sheet. Information becoming available after finalisation of this document will be evaluated in the review process of priority substances according to Art. 16(4) of the Water Framework Directive. If necessary, the Environmental Quality Standard substance data sheets will then be revised in the light of technical and scientific progress.

3 1 Identity of substance Priority Substance No: 15 Fluoranthene CAS-No: Classification WFD Priority List * : PS * PS: priority substance; PHS: priority hazardous substance; PSR: priority substance under review according to Decision 2455/ Proposed quality standards 2.1 Overall quality standards Ecosystem Quality Standard Quality Standard rounded values AA-QS all types of surface waters covered by the WFD 0.09 µg/l corresponding conc. in: freshwater SPM 1069 µg/kg dry wt saltwater SPM 1247 µg/kg dry wt 0.1 µg/l corresponding conc. in: freshwater SPM 1100 µg/kg dry wt saltwater SPM 1200 µg/kg dry wt Comment: MAC-QS (ECO) 0.9 µg/l 1 µg/l see section 8.1 The suggested overall QS is referring to the protection of the benthic community (see 8.2 & 8.6). 2.2 Specific quality standards Protection Objective # Quality Standard Comment: Pelagic community (freshwater and saltwater) Benthic community (sediment) Predators (secondary poisoning) Food uptake by man Abstraction of water intended for human consumption (AWIHC) Water intended for human consumption (WIHC) # 0.12 µg/l corresponding conc. in: freshwater SPM 1425 µg/kg dry wt saltwater SPM 1662 µg/kg dry wt 0.09 µg/l corresponding conc. in: freshwater SPM 1069 µg/kg dry wt saltwater SPM 1247 µg/kg dry wt mg/kg prey (wet wt) the corresponding concentration in water is most probably higher than the suggested overall QS (>0.09 µg/l) derivation of QS not required (also insufficient availability of toxicity data) 0.2 µg/l see section 8.1 see section 8.2 BCF values cover a wide range, the potenitial for biomagnification is not known; however scenario calculations suggest that the proposed overall QS is protective for predators as well; see section 8.3 see section 8.4 A-1 value for ΣPAH in CD 75/440/EEC see section Fluoranthene is not covered by the limit value set in CD 98/83/EC for the sum of certain PAHs; see section 8.5 If justified by substance properties or data available, QS for the different protection objectives are given independently for freshwater environments, transitional waters or coastal and territorial waters - 1 -

4 3 Classification R-Phrases and Labelling Reference: This chemical substance is not classified in the Annex I of Directive 67/548/EEC. [15] 4 Physical and chemical properties Property Value: Master Ref: Ref. in master ref. & comments: Mol. Weight: g/mol [6] Water Solubility mg/l (25 C) [6] [24], [33] Vapour Pressure: 0,7 x 10-3 Pa (20 C); 1,3 x 10-3 Pa (25 C); 6 x 10-6 mm Hg (20 C) [33] [6] [33], [35] 5 Environmental fate and partitioning Property Value: Master Ref: Abiotic degradation Hydrolysis Biodegradation Partition coefficients log Kow (octanol water) Hydrolysis not probable; stable under environmental conditions [6] [41] [37] [6] [5] Ref. in master ref. & comments: [10], [33], [35] Koc (organic carbon-water) Aquifer u L/kg Sediment L/kg (calculated) L/kg [6] [36] [37] [38], [39] Bioaccumulation BCFs: Fish Crustacea (Daphnia magna) Mollusca (Crassostrea virginica) Sediment log Koc log Koc 5.16 used in [5] 1,700 (calculated) 1,740 10,000 l/kg [5] [6] [33] [4] [33] Refs. in appendix 5 of [5] - 2 -

5 6 Effect data (aquatic environment) Table 6.1: Overview on toxicity data of most sensitive species from different sources (master reference) (*: fw = freshwater, sw = saltwater) Species Taxon. Grp. Medium * Duration Effect Endpoint Value Unit Master Ref. Reference in master ref. Freshwater Ceriodaphnia dubia Crustacea fw 7 d Reproduction, EC µg/l [7] Mortality Scenedesmus subspicatus Alga fw 7 d Growth EC µg/l [6] Kördel et al [23] Brachydanio rerio Pisces fw 41 d Growth, as fish NOEC 6.9 µg/l [5], [6] Hooftman et al length Growth, as wet NOEC 22 µg/l weight Mortality NOEC 69 µg/l Pseudokirchneriella subcapitata Alga fw 72 h Growth EC µg/l [7] Daphnia magna Crustacea fw 21 d Reproduction NOEC 15 µg/l [6] Kördel et al [23] Hyallela azteca Crustacea fw 10 d Mortality NOEC 18 µg/l [7] Suedel et Rodgers (1996) Chironomus tentans Insecta fw 10 d Mortality NOEC 30 µg/l [7] Suedel et Rodgers (1996) Lemna gibba Planta fw 8 d Growth NOEC 500 µg/l [7] Ren et al. (1994) Rana catesbeiana Amphibia fw 4 d Behaviour NOEC 11 µg/l [7] Walker et al. (1998) Pimephales promelas Pisces fw 5 min Avoidance NOEC 8.6 µg/l [7] Farr et al. (1995) Scenedesmus subspicatus Alga fw 7 d Growth EC50 12 µg/l [6] Kördel et al [23] Daphnia magna Crustacea fw 10.8 hours Mortality LC50 9 µg/l [1] Newsted and Giesy (1987) Gammarus pulex Crustacea fw 14 day Mortality LC50 96 mg/l [1] Boxall (1996) Ictalurus punctatus Pisces fw 4 d Mortality LC50 36 µg/l [6] Gendusa 1990 [19] Sediment, freshwater Rhepoxynius abronius Crustacea fw, interstitial 10 d Mortality NOEC 12 µg/l [7] Swartz et al. (1989) Hyallela azteca Crustacea fw, sediment 10 d Mortality NOEC < 12.9 mg/kg dw [7] Suedel et Rodgers (1996) Chironomus tentans Insecta fw, sediment 10 d Mortality NOEC 13.9 mg/kg dw [7] Suedel et Rodgers (1996) Diporeia sp. Crustacea fw, sediment 30 d Mortality NOEC < 15.6 mg/kg dw [8] Driscoll et al. (1997) Stylaria lacustris Annelida fw, sediment 10 d Mortality NOEC 26.8 mg/kg dw [7] Suedel et Rodgers (1996) Rhepoxynius abronius Crustacea fw, sediment 10 d Mortality LC mg/kg dw [8] Swartz et al. (1990) Corophium spinicorne Crustacea fw, sediment 10 d Mortality LC mg/kg dw [8] Swartz et al. (1990) Saltwater Mytilus edulis Mollusca sw 7 d Immunocompetence NOEC 20 µg/l [7] Coles et al. (1994) Grandidierella japonica Crustacea sw 96 h Behaviour EC50 27 µg/l [6] Boese et al [17] Neanthes arenaceodentata Annelida sw 96 h Mortality LC µg/l [5] Rossi & Neff 1978 Mulinia lateralis Mollusca sw 96 h Larval growth in fluorescent ligth EC µg/l [6] Pelletier et al [29] - 3 -

6 Table 6.2: Mammal oral toxicity data relevant for the assessment of non compartment specific effects relevant for the food chain (secondary poisoning) [9] Species Mus musculus Mouse Duration Endpoint 13 wk NOAEL, based on: nephropathy, increased liver weights, haematological alterations, and other clinical effects mg/kg bw d Reference 125 U.S. EPA Week mouse oral subchronic toxicity study. Prepared by Toxicity Research Laboratories, Ltd., Muskegon, MI for the Office of Solid Waste, Washington, DC. 104 pp (TRL Study No ) 6.2 Summary on endocrine disrupting potential Effects of fluoranthene on endocrine regulation are not mentioned in [2]. 7 Effect data (human health) Table 7.1: Effect data relevant to human health aspects Effect Summarised information chronic oral toxicity: [13] US-EPA oral reference dose (RfD): 40 µg/kg bw/ day, based on a 13 wk study with mice. The NOAEL: of this study is 125 mg/kg bw/d and the LOAEL 250 mg/kg bw/d. Critical effects were nephropathy, increased liver weights, and changes in clinical and hematological parameters. The uncertainty factor used to derive the RfD is This UF reflects 10 each for intra- and interspecies variability, 10 for the use of a subchronic study for the derivation of a chronic RfD, and 3 for lack of supporting reproductive/developmental toxicity and toxicity data in a second species. [13] mutagenicity: Experimental results are ambigous. Positive and negative results have been observed with different strains of Salmonella thyphimurium. Positive and negative results have also been obtained with hamster cells. A test with human lymphoblasts was positive. [7] cancerogenicity: Experimental results on cancerogenicity have been judged insufficient. In the absence of data on humans fluoranthene has been classified as non carcinogenic for humans (class D, IARC 1983, cited in [7] )

7 8 Calculation of quality standards 8.1 Quality standards for water Long-term as well as short-term toxicity data are available for freshwater and marine species, respectively. On the basis of the available data no apparent differences in the sensitivity of freshwater or saltwater organisms can be identified. Therefore it is suggested to use the combined data set for the derivation of quality standards for both freshwater and saltwater environments. Freshwater NOECs (or EC10 values as NOEC surrogates) are available for algae, plants, crustaceans, fish, amphibians, insects and molluscs. The lowest NOEC is 1.2 µg/l (EC10 of Ceriodaphnia dubia). As NOECs for species of at least three different trophic levels are available the appropriate assessment factor is 10 [4]. QS freshwater = 0.12 µg Fluoranthene /l An experimental Kp susp is not available. But the Kp susp can be calculated based on the Koc as described in the TGD (section ) [3]. It is proposed to use log Koc 5.16 for the calculation. It was used in the Netherlands for the calculation of the MPC for fluoranthene [5] and it can be regarded as a mean of the Koc range cited in the available reports (see section 5 of this data sheet). Kp susp [l/kg] = foc (0.1) * Koc (144,544) = 14,454 l/kg As the log Kp susp is >3, the trigger to calculate the corresponding concentration to the QS freshwater in SPM is met and therefore QS SPM.freshwat is derived (see section of the final report [4] ). QS freshwater [0.12 µg/l] QS SPM.freshwat = = 1425 µg/kg SPM (dry wt) C SPM [15 mg/l] * 10-6 [kg/mg] + Kp -1 [(14,454 l/kg) -1 ] Transitional, coastal and territorial waters Long-term tests with freshwater species from more than 3 different taxonomic groups and tests with additional marine taxonomic groups (marine annelids and molluscs) are available. The marine species have comparable sensitivities to the freshwater species (this was also the general conclusion drawn from a comparison of freshwater and saltwater toxicity data of several PAHs [5] ). Thus, it is suggested, in accordance with the provisions of the TGD to pool the data and set the same quality standard for saltwater as derived for freshwater: QS saltwater = QS freshwater As the log Kp susp is >3, the corresponding concentration to the QS saltwater in SPM is calculated (see section of the Manual [4] ). For the TGD standard water, the concentration corresponding to the QS saltwater is that calculated for freshwater (see above). However, the SPM concentration in marine waters is significantly lower than in freshwater (discussed in the context of the marine risk assessment: approx. 3 mg/l as standard concentration). Therefore, the quality standard is, as an example, also calculated for a SPM concentration of 3 mg/l: - 5 -

8 QS freshwater [0.12 µg/l] QS SPM.saltwat = = 1662 µg/kg SPM (dry wt) C SPM [3 mg/l] * 10-6 [kg/mg] + Kp -1 [(14,454 l/kg) -1 ] Quality standard accounting for transient concentration peaks (MAC-QS) Acute toxicity data are available for freshwater and marine organisms of different taxonomic groups (algae, crustacea, fish, annelida, mollusca). The lowest short-term acute toxicity value 1 is the Daphnia magna 10.8 h LC50 of 9 µg/l (Newsted amd Giesy, 1987 cited by [1] ). The MAC-QS is derived on the basis of this LC50 and the guidance given in the TGD on the effects assessment for intermittent releases (section of the Manual [4] ). As the available short term toxicity data cover a wider range of different taxonomic groups it is suggested to use only a reduced assessment factor of 10 (instead of 100). MAC-QS = 0.9 µg Fluoranthene / l The derivation of a separate MAC-QS applicable to transient concentration peaks in coastal and territorial waters is not required as it is not probable that significant peaks occur in these waters. For transitional waters the freshwater MAC-QS may be used. 8.2 Quality standard for sediment As the log Kp susp is >3, the calculation of a quality standard for sediment is required (see table 1a of the Manual [4] ). Several tests with different freshwater sediment organisms (belonging to the taxa crustacea, insecta and annelida) are available. Thus, according to the TGD, the QS for sediment should be calculated by both the assessment factor method and the equilibrium partitioning method Equilibrium partitioning method The equilibrium partitioning approach only considers uptake via the water phase. However, uptake may also occur via other exposure pathways like ingestion of sediment and direct contact with sediment. There is evidence from studies in soil that the proportion of the total dose remains low for chemicals with a log Kow up to 5. For compounds with a log Kow greater than 5 the equilibrium method is used in a modified way. It is recommended in the TGD to increase the PEC sed /PNEC sed ratio by a factor of 10 for the risk assessment. However division of the PNEC water by a factor of 10 will result in the same ratio. Thus, it can be inferred that division of the QS water by a factor of 10 will result in a tentative QS sediment that accounts for possible uptake via the mentioned additional routes of exposure. As the available log Kow.s of fluoranthene are in the range of the QS water is divided by a factor of 10. It is proposed to use log Kow 5.16 for the assessment (see section 5 of this data sheet, kind of intermediate). 1 In [6] two results (EC and 900 µg/l) differing by a factor more than 1000 for acute tests with the marine mollusc Mulinia lateralis are cited (see table 6.1 of this data sheet). No explanation on possible reasons for this huge difference is given in [6]. Therefore the results are not considered for the derivation of the MAC-QS

9 Kp SPM-water [3,614 m 3 /m 3 ] QS sed.wet_weight [mg.kg -1 ] = * 1,000 * QS water [ mg/l] * 10-1 bulk density SPM.wet [1,150 kg/m 3 ] with: K SPM-water = f solid (0.1) * Kp susp (14,454 l/kg) / 1,000 * RHO solid (2,500 kg/m 3 ) = 3,614 m 3 /m 3 (section of [3] ) bulk density SPM.wet = 1,150 kg/m 3 1,000 = conversion factor m 3 /kg to l/kg 10-1 = factor to account for possible additional uptake routes for substances with log Kow >5 The TGD defines wet SPM as 90% vol/vol water (density 1 kg/l) and 10% vol/vol solids (density 2.5 kg/l), thus giving a wet density of (0.9 1) + ( ) = 1.15 kg/l. The dry weight of solids is therefore 0.25 kg (per litre wet SPM) and thus the wet:dry ratio is 1.15/0.25 = 4.6. This results in the following quality standard for both freshwater and marine sediment (wet and dry weight): QS sediment 37.7 µg/kg (wet wt) 173 µg/kg (dry wt) Assessment factor method There are 6 subchronic tests with sediment dwelling organisms from 3 different taxonomic groups (crustacea, insecta, annelida) available (see table 6.1). Endpoints are either NOECs or LC50s, for the most sensitive species only a LC50 is available. The TGD foresees the use of 1000 as assessment factor for short-term acute tests and factors of for long-term NOECs/EC10s, depending on the quantity and quality of the data available. Because the 4 NOECs available refer to subchronic rather than to real long-term exposure and because there is no NOEC available for the most sensitive species, it is proposed to use an AF of 100 to derive the QS sediment based on the lowest NOEC (which might be rather considered as LOEC) 2 : QS sediment = NOEC (<12.9 mg/kg) / AF 100 = 129 µg Fluoranthene /kg sediment (dry weight) The quality standard derived on the basis of experimental findings is very similar to the corresponding value derived with the Equilibrium Partitioning method. Therefore it is suggested to adopt the toxicity test based QS as QS sediment. The TGD normally foresees to apply more stringent assessment factors for the marine effects assessment in case toxicity data referring to marine organisms are not available (which is the case with regard to tests with marine sediment organisms). However, as tests with pelagic marine taxonomic groups show comparable sensitivities to the pelagic freshwater species, it appears reasonable to assume that the sensitivity of freshwater and saltwater sediment organisms towards fluoranthene is as well not significantly different. It is therefore suggested to set the same quality standard for marine sediment as derived for freshwater sediment Calculation of a water concentration corresponding to the QS sediment As the QS sediment is based on real sediment data (i.e. was not derived by transforming water concentrations with the Equilibrium Partitioning method), it is necessary to calculate the 2 The TGD does not provide conclusive guidance regarding the appropriate size of the AF for a data set as available for fluoranthene - 7 -

10 corresponding concentration in water. To this end, the equilibrium partitioning equation is used (see 8.2.1): QS sediment.wwt [28 µg/kg] bulk density SPM.wet [1,150 kg/m 3 ] QS water = * = 0.09 µg Fluoranthene /l 1,000 * 0.1 Kp SPM-water [3,614 m 3 /m 3 ] with: K SPM-water = f solid (0.1) * Kp susp (14,454 l/kg) / 1,000 * RHO solid (2,500 kg/m 3 ) = 3,614 m 3 /m 3 (section of [3] ) bulk density SPM.wet = 1,150 kg/m 3 1,000 = conversion factor m 3 /kg to l/kg 10-1 = factor to account for possible additional uptake routes for substances with log Kow >5 QS sediment.wwt = 129 [µg/kg dw] / 4.6 = 28 µg/kg ww The TGD defines wet SPM as 90% vol/vol water (density 1 kg/l) and 10% vol/vol solids (density 2.5 kg/l), thus giving a wet density of (0.9 1) + ( ) = 1.15 kg/l. The dry weight of solids is therefore 0.25 kg (per litre wet SPM) and thus the wet:dry ratio is 1.15/0.25 = 4.6. The water concentration corresponding to the QS sediment is lower than the quality standard derived for the protection of the pelagic community. Therefore, the value of 0.09 µg fluoranthene /l is suggested as water quality standard. QS freshwater = QS saltwater = 0.09 µg Fluoranthene / l The corresponding concentrations in SPM are calculated as follows (see 8.1 for details): QS freshwater [0.09 µg/l] QS SPM.freshwat = = 1069 µg/kg SPM (dry wt) C SPM [15 mg/l] * 10-6 [kg/mg] + Kp -1 [(14,454 l/kg) -1 ] QS freshwater [0.09 µg/l] QS SPM.saltwat = = 1247 µg/kg SPM (dry wt) C SPM [3 mg/l] * 10-6 [kg/mg] + Kp -1 [(14,454 l/kg) -1 ] 8.3 Secondary poisoning of top predators BCFs up to 10,000 have been found for fluoranthene. Thus the derivation of a quality standard referring to secondary poisoning is required. As follow-up to the Workshop of the Expert Group on Quality Standards (12-16 May, Brussels), France submitted a NOAEL obtained for mice that is suitable to derive a QS referring to secondary poisoning (see tab. 6.2). According to the TGD (table 22 of [3] ), the 90 d NOAEL of 125 mg/kg d can be converted into a NOEC by multiplying it with a body weight / daily food intake conversion factor of 8.3: NOEC food = 125 * 8.3 = mg fluoranthene /kg food The appropriate assessment factor to derive the PNEC ( QSsecpois.biota) based on a NOEC food of a subchronic 90 d study is 90 (table 8 of [4] ). QS secpois.biota = NOEC food ( mg/kg) / AF 90 = mg/kg prey (wet wt) - 8 -

11 Reported BCF values for fish and crustaceans are in the range of 1,740 (see section 5) but the BCF reported for the oyster Crassostrea virginica is considerably higher (10,000). Information the potential for biomagnification (i.e. BMF figures) is not available for fluorathene. According to the provisions given in the TGD [3], biomagnification factors (BMF) shall be taken into account when assessing the risk for secondary poisoning. Ideally the BMF shall be based on measured data but if such data are not available the use of default values is recommended. These default values are defined in the TGD based on the Kow or the BCF of the substance (see sections and of the TGD [3] for details). For substances with a BCF < 2000 no BMF factors need to be considered whereas for substances with a BCF >5000 the use of a default BMF of 10 is suggested for freshwater environments and for marine environments the use of a BMF of 100 (10*10). The higher default BMF for the marine environment is recommended in order to take account of the more complex and longer trophic pathways in marine ecosystems. Some scenario calculations may highlight the potential of fluoranthene for secondary poisoning (table 8.1). The QS secpois.water is calculated as follows: QS secpois.water = QS secpois.biota (11.53 [mg/kg prey]) / BCF * BMF Table 8.1: Scenario calculations for "safe" water concentrations with respect to secondary poisoning Scenario BCF BMF freshwater BMF marine QS secpois.freshw QS secpois.saltw Fish/Crustaceans 1,740 No TGD default No TGD default 6.63 µg/l 6.63 µg/l as prey Crassostrea as prey 10, (TGD default) Crassostrea as prey (without default BMFs) 100 (TGD default) 0.15 µg/l µg/l 10, µg/l 1.15 µg/l From the figures calculated in table 8.1 it can be concluded that the water based quality standard required to protect the benthic community (0.09 µg/l) is also suitable to protect predators from secondary poisoning. The default BMFs recommended by the TGD are precautionary and it is therefore not very probable that biomagnification up to a factor of 100 occurs in the field. Further, as mussels are filter feeders, the reported BCF of Crassostrea may already partially be due to biomagnification. 8.4 Quality standard referring to food uptake by humans Fluoranthene is not classified with regard to human health. Therefore it is not required to derive a quality standard referring to the protection of human health from adverse effects due to the ingestion of fishery products (trigger criteria not met)

12 8.5 Quality standard for drinking water abstraction The "A1 value" for PAHs (sum) set in the context of Council Directive 75/440/EEC is 0.2 µg/l. Fluoranthene is not covered by the limit value set in Council Directive 98/83/EC for the sum of certain PAHs. Fluoranthene is not classified with regard to human health. Therefore it is not required to derive a provisional drinking water standard (trigger criteria not met). 8.6 Overall quality standard For polyaromatic hydrocarbons, the SCTEE recommended to use a group approach both for the quality standards referring to ecological protection objectives as well as to human health [14]. However, with the current scientific knowledge on environmental behaviour, fate and effects it is not possible to develop such an approach. Therefore, although the proposal of the SCTEE is in principle supported, the quality standard proposals must at present be based on information / data available for the individual PAH-compounds. It is suggested to adopt as overall annual average quality standard (AA-QS) the specific standard derived for the protection of sediment dwelling organisms. If the setting of a specific MAC-QS in areas designated for the abstraction of water intended for human consumption (AWIHC) in accordance with Art. 7 of the WFD is required, that MAC-QS (AWIHC) should be < 0.2 µg/l

13 9 References [1] UK response to request for information relating to quality standards for the Priority List. Submission of data on toxicity, persistence and bioaccumulation by DETR ( of 23 May 2001 by Natasha Robinson) [2] COM(2001)262 final: Communication from the Commission to the Council and the European Parliament on the implementation of the Community Strategy for Endocrine Disrupters a range of substances suspected of interfering with the hormone system of humans and wildlife. (Table 2: substances with evidence of ED or evidence of potential ED which are neither restricted nor currently being addressed under existing Community legislation. Table 3: Substances with evidence of ED or evidence of potential ED, already regulated or being addressed under existing legislation. Table 4: Substances with insufficient data in the BKH Report) [3] Technical Guidance Document on Risk Assessment in Support of Commission Directive 93/67/EEC on Risk Assessment for New Notified Substances and Commission Regulation (EC) No 1488/94 on Risk Assessment for Existing Substances and Directive 98/8/EC of the European Parliament and the Council Concerning the placing of biocidal products on the market. Part II. European Commission Joint Research Centre, EUR EN/2, European Communities Available at the internet-site of the European Chemicals Bureau: [4] Manual of the Methodological Framework Used to Derive Environmental Quality Standards for Priority Substances of the Water Framework Directive. Peter Lepper, Fraunhofer-Institute Molecular Biology and Applied Ecology, 15 November Available at the internet-site of the European Commission: [5] Kalf, DF et al., 1995: Integrated Environmental Quality Objectives for Polycyclic Aromatic Hydrocarbons [PAHs). National Institute of Public Health and the Environment, Bilthoven, The Netherlands. RIVM Report no [6] Frimmel, FH et al., 2001: Ableitung von Qualitätszielen für Kandidatenstoffe der prioritären Liste für die EU-Wasserrahmenrichtlinie. Projektbericht zum Forschungsvorhaben. Stoffdatenblatt für Fluoranthen. [7] Vindimian et al : Complément au SEQ-Eau : méthode de détermination des seuils de qualité pour les substances génotoxiques. Rapport final. Client : Agence de l eau Rhin Meuse. [8] Comments of Germany received after the meeting of the Expert Group on Quality Standards (Brussels, May 2003). by Dieter Schudoma, German EPA, [9] Comments of France received after the meeting of the Expert Group on Quality Standards (Brussels, May 2003). by Vincent Bonnomet, INERIS, [10] Suedel, BC., Rodgers, J.H. 1996: Toxicity of Fluoranthene to Daphnia magana, Hylella azteca, Chironomus tentans, and Stylaria lacustris in Water-Only and Whole Sediment Exposures. Bull. Environ. Contam. Toxicol. 57 : [11] Driscoll, S.K. et al. 1997: Accumulation and Toxicity of Fluoranthene in Sediment Bioassays with Freshwater Amphipods. Environ. Toxicol. Chem. 16, [12] Swartz, R.C. 1990: Toxicity of Fluoranthene in Sediment to Marine Amphipods: A Test of the Equilibrium Partitioning Approach to sediment Quality Criteria. Environ. Toxicol. Chem. 9, [13] Fluoranthene, CASRN ; Reference Dose for Chronic Oral Exposure. Last Revisited 07/01/1993. U.S. Environmental Protection Agency Integrated Risk Information System (IRIS). [14] Opinion of the Scientific Committee on Toxicity, Ecotoxicity and the Environment (SCTEE) on The Setting of Environmental Quality Standards for the Priority Substances included in Annex X of Directive 2000/60/EC in Accordance with Article 16 thereof, adopted by the CSTEE during the 43 rd plenary meeting of 28 May 2004, European Commission Health & Consumer Protection Directorate General, Brussels. [15] ESIS: European Chemicals Bureau ESIS (European Substances Information System), January tick ESIS button, then enter CAS or EINECS number of substance