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APPENDIX VIII Multimedia fate models can be used to estimate exposure to metals. However, there are several differences compared to the use of these models for organic compounds. Below, differences are described for applying regional models. Reference is made to the sections in the main text. 1. Physico-chemical properties (section 2.3.2) In general water solubility, boiling point and vapour pressure cannot be used. The octanol-water partitioning coefficient is not appropriate and measured partition coefficients Kp should be used instead. 2. Partition coefficients (section 2.3.5) Adsorption to aerosol particles Most of the metal present in the atmosphere will be bound to aerosols. Therefore, an extremely low value for the vapour pressure should be used in formula 5 on page 31, e.g. 10-20 Pa. This leads to a value for Fassaer almost equal to one. If a valid measured value is available, this value can be used. Volatilisation Volatilisation can be ignored for metals, except for mercury-compounds and several organometallo compounds. Therefore the Henry-coefficient should be set to a very low value (formula 6). Adsorption/desorption Formula 8 and 9 cannot be used. As stated in this appendix, measured Kp values must be used for water-soil, water-sediment and water-suspended matter. 3. Biotic and abiotic degradation rates (Section 2.3.6) Not important for regional models. 4. Elimation processes prior to the release in the environment (Section 2.3.7) For applying models like SimpleTreat a partition coefficient is used for water-sludge. For metals a measured Kp value must be used. However, it should be noted that Kp values are different for the different metal species. 5. Calculation of PECregional (Section 2.3.8.7) The values applied for model parameters for the regional model (Table 10), intermedia mass transfer coefficients (Table 11) and model parameters for the continental concentration (Table 12) can be used. Figure 1: Use of multimedia fate models for metals 306
In a natural soil or sediment system, metals can be distributed over the following fractions: • dissolved in the pore water, • reversibly or irreversibly bound to soil or sediment particles, • reversibly or irreversibly bound to organic ligands, • encapsuled in secondary clay minerals and metal(hydr)oxides, • encapsuled in the primary minerals. APPENDIX VIII It is recognised that for various organisms, only the metal species present in the aqueous phase (pore water) are potentially available for direct uptake by biota and thus mainly responsible for effects on biota. Other uptake routes may also be important, especially for metals with high Kp values, but at the moment little is known on how to treat these processes quantitatively in the risk assessment. Processes determining the availability of metals for direct uptake by biota from the aqueous phase include precipitation, dissolution, adsorption, desorption and complexation. All processes mentioned are not only pH-dependent (adsorption of metal cations for instance increases with pH), but are also strongly influenced by competition for adsorption sites and to all complexation reactions likely to increase the solubility of the metal. At the moment most Kp values are expressed in terms of total concentrations present in both the aqueous and the solid phase. As can be derived from the possible distribution sites for metals mentioned above, availability of metals for uptake by biota can differ from site to site and, due to amongst others weathering and (de)sorption processes, may change over time. At this stage it is of importance to realise that in general the bioavailability of metals in test systems (expressed as the fraction of the total amount of metal present in the system) may be higher than the bioavailability under field conditions. When performing risk assessment it is of utmost importance that both PEC and PNEC are based on similar levels of availability. What is required is that for both exposure and effect assessment, Kp values are expressed in terms of concentrations available for uptake by biota in both the aqueous and the solid phase: K p = total available concentration in solid phase concentration in aqueous phase It is of importance to be aware that equation 1 differs from the commonly used expressions for Kp in the sense that instead of total concentrations in both the solid and liquid phase, available concentrations are to be used. Reason for this is that part of the metal present in the solid phase may be incorporated in the mineral fraction and is therefore not available. Several experimental extraction techniques have been developed to determine available concentrations of metals, thus enabling the calculation of Kp values according to equation (1). However, up till now the underlying concepts for a standardised approach towards partition coefficients representing availability have not yet been sufficiently worked out. Finally, with regard to availability of metals it should be noted that apart from the general processes denoted above, under certain environmental conditions additional complexation and precipitation processes may take place that may strongly diminish aqueous metal concentrations. An example of such a process is the formation of insoluble metalsulphides under anaerobic conditions (the so-called Acid Volatile Sulphide, or AVS-concept). (1) 307
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Institute for Health and Consumer P
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LEGAL NOTICE Neither the European C
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OVERVIEW This Technical Guidance Do
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CONTENTS 1 GENERAL INTRODUCTION ...
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4.2.3.4 Use of biodegradation scree
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1 GENERAL INTRODUCTION 1.1 BACKGROU
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GENERAL INTRODUCTION countries in t
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GENERAL INTRODUCTION PNEC is regard
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2 ENVIRONMENTAL EXPOSURE ASSESSMENT
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ENVIRONMENTAL EXPOSURE ASSESSMENT r
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2.2 MEASURED DATA ENVIRONMENTAL EXP
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ENVIRONMENTAL EXPOSURE ASSESSMENT w
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ENVIRONMENTAL EXPOSURE ASSESSMENT o
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ENVIRONMENTAL EXPOSURE ASSESSMENT T
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ENVIRONMENTAL EXPOSURE ASSESSMENT r
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Production ENVIRONMENTAL EXPOSURE A
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Back to processing Product at end o
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ENVIRONMENTAL EXPOSURE ASSESSMENT s
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Explanation of symbols ENVIRONMENTA
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ENVIRONMENTAL EXPOSURE ASSESSMENT s
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ENVIRONMENTAL EXPOSURE ASSESSMENT U
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ENVIRONMENTAL EXPOSURE ASSESSMENT a
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ENVIRONMENTAL EXPOSURE ASSESSMENT F
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2.3.5.1 Adsorption to aerosol parti
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ENVIRONMENTAL EXPOSURE ASSESSMENT I
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2.3.6.1 Hydrolysis ENVIRONMENTAL EX
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2.3.6.3 Photochemical reactions in
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constant of zero. However, if it ca
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ENVIRONMENTAL EXPOSURE ASSESSMENT A
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ENVIRONMENTAL EXPOSURE ASSESSMENT a
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Primary Settler Aeration Tank 2 5 3
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ENVIRONMENTAL EXPOSURE ASSESSMENT I
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ENVIRONMENTAL EXPOSURE ASSESSMENT d
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ENVIRONMENTAL EXPOSURE ASSESSMENT e
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Table 10 Overview of different expo
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ENVIRONMENTAL EXPOSURE ASSESSMENT -
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2.3.8.3 Calculation of PEClocal for
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ENVIRONMENTAL EXPOSURE ASSESSMENT W
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Guidance for calculating PEClocal i
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Concentration (% of initial) 160 14
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Calculation of PEClocalsoil For soi
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ENVIRONMENTAL EXPOSURE ASSESSMENT
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Output ENVIRONMENTAL EXPOSURE ASSES
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3 EFFECTS ASSESSMENT 3.1 INTRODUCTI
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3.2.1.1 Completeness of data New su
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EFFECTS ASSESSMENT • it is clearl
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EFFECTS ASSESSMENT 3.3 EFFECTS ASSE
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Table 16 Assessment factors to deri
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Input data EFFECTS ASSESSMENT The m
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Estimation of the PNEC The PNEC is
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EFFECTS ASSESSMENT biodegradability
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Table 17 Test systems for derivatio
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EFFECTS ASSESSMENT representative o
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In the partitioning method, it is a
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EFFECTS ASSESSMENT As mentioned in
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3.6.2.1 Calculation of PNEC using t
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3.7 EFFECTS ASSESSMENT FOR THE AIR
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EFFECTS ASSESSMENT procedure availa
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EFFECTS ASSESSMENT bioaccumulation
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EFFECTS ASSESSMENT For some chemica
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EFFECTS ASSESSMENT i.e. without enh
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Conversion factors for laboratory a
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EFFECTS ASSESSMENT • relative sen
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EFFECTS ASSESSMENT Earthworms are a
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MARINE RISK ASSESSMENT environment
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MARINE RISK ASSESSMENT of equal rel
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4.2.3.3 Marine biodegradation simul
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MARINE RISK ASSESSMENT In addition
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Explanation of symbols MARINE RISK
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MARINE RISK ASSESSMENT evaluate the
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MARINE RISK ASSESSMENT marine water
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MARINE RISK ASSESSMENT The addition
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MARINE RISK ASSESSMENT Statistical
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MARINE RISK ASSESSMENT sediment, fo
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Table 27 Assessment factors for der
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Table 28 continued Acute and chroni
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MARINE RISK ASSESSMENT of different
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MARINE RISK ASSESSMENT • a measur
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MARINE RISK ASSESSMENT b. the conce
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MARINE RISK ASSESSMENT mechanisms s
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MARINE RISK ASSESSMENT The use of t
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4.4.4.2 Assessment of measured BCF
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MARINE RISK ASSESSMENT required to
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Table 33 Overview of PEC/PNEC ratio
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RISK CHARACTERISATION If a refineme
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Classified dangerous to the Environ
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RISK CHARACTERISATION eaters. This
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6 TESTING STRATEGIES 6.1 INTRODUCTI
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TESTING STRATEGIES Performance of a
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TESTING STRATEGIES Care must be tak
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Algal testing Algae toxicity test (
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TESTING STRATEGIES • long-term te
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Microbial assays TESTING STRATEGIES
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TESTING STRATEGIES A soil bioassay
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REFERENCES Brandes LJ, den Hollande
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REFERENCES IPCS (2000). Framework f
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REFERENCES OECD (1984f). Activated
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REFERENCES Pack S. (1993). A review
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REFERENCES US EPA (1996). Whole Sed
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APPENDIX I volume imported in the E
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APPENDIX I MC IV “Wide dispersive
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APPENDIX I 210 Stage Main category
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APPENDIX I the number of days over
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APPENDIX I Stage Main category Ia I
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APPENDIX I manufacturing of motor c
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APPENDIX I 1. extension of the tabl
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APPENDIX I 220 A-tables Estimates f
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APPENDIX I PRIVATE USE Not applicab
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APPENDIX I IC = 3: CHEMICAL INDUSTR
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APPENDIX I IC = 5: PERSONAL /DOMEST
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APPENDIX I Table A4.1 continued Com
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APPENDIX I IC = 7: LEATHER PROCESSI
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APPENDIX I IC = 9: MINERAL OIL AND
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APPENDIX I WASTE TREATMENT Table A5
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APPENDIX I For the emission factors
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APPENDIX I INDUSTRIAL USE Table A3.
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APPENDIX I INDUSTRIAL USE Table A3.
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APPENDIX I PRIVATE USE Table A4.5 C
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APPENDIX I PRIVATE USE Table A3.16
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APPENDIX I 246 B-tables Estimates f
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APPENDIX I FORMULATION Table B2.2 f
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APPENDIX I IC = 3: CHEMICAL INDUSTR
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APPENDIX I IC = 5: PERSONAL/DOMESTI
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APPENDIX I IC = 7: LEATHER PROCESSI
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