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APPENDIX VIII collection), and that is generally considered to be a better estimate for the fraction that is potentially available for organisms than the total concentration; • bioavailable fraction: the fraction that is available for uptake by a specific organism. A single substrate has only one 'availability' for each of the possible physico-chemical extraction procedures. The bioavailability differs, however, per biological species. Thus, taking soil as an example, for instance for worms in a certain soil the bioavailability may be high (it is in this case the concentration in the pore water that determines uptake), while for arthropods in the same soil the bioavailability may be low (uptake by the food is for these organisms the dominant uptake route); • natural background concentration: the concentration that is present due to natural causes only; • ambient background concentration: the concentration that is present due to natural background plus the immission of metals from diffuse sources of human origin 9. For soils or sediments • water extractable fraction or concentration: the fraction or the concentration of the metal that is extracted after shaking the substrate in aqueous solution (usually distilled water); • neutral-salt solution extractable fraction or concentration: the fraction or the concentration of the metal that is extracted after shaking the substrate in neutral salt solution; • pore water concentration: the concentration of the metal that is present in the pore water collected from the substrate; • pore water activity: the concentration of a metal in the aqueous fraction that is potentially biologically active (usually considered to be the concentration of metal ions that can be taken up by organisms). Exposure assessment For the assessment of metals it is in general necessary to take into account all metal species that are emitted to the environment which in the end lead to concentrations of the bioavailable species that may cause effects. In practice, a limited number of major emissions or uses predominate and these must initially be identified. The assessment will normally concentrate on the impact of these emissions since they will be the major contributors to the regional burden, but due care must be paid to the impact of local emissions of specific substances. An inventory of all relevant emission sources must be prepared and specific industry and use categories identified for assessment of both local and regional impact. Two types of emission can be identified: diffuse emissions and point source emissions. For some metal compounds, diffuse sources such as emissions from agriculture, transport, corrosion etc 9 In case of soil, for all metals so-called reference lines were derived by correlating measured ambient background concentrations (total concen-trations in the soil-matrix) at a series of remote rural sites in the Netherlands to the percentage lutum (%L) and the organic matter content (%H) of these soils (Ministry of VROM, 1994). The same approach has been followed in Flanders, Belgium (Ontwerp uitvoeringsbesluit, 1995). To this end the 90percentiles of the ambient background concentrations measured were used. The metal-specific parameters of the regression equations represent the strength of binding of the different metals to soils of different clay and humus contents. The reference lines are not only used to calculate ambient background concentrations at given sites, but also to enable the extrapolation of laboratory toxicity data to standard-soil conditions. Some typical examples of reference lines derived in The Netherlands ([ ] = ambient background concentration in mg/kg soil, L = % lutum, H = % organic matter): [Cu] = 15 + 0.6 . (L + H) ; [Zn] = 50 + 1.5 . (2L + H) or [Ni] = 10 + L. 302
APPENDIX VIII can make a significant contribution to the overall levels. For many substances, however, local emissions from point sources will need to be considered as well as the wider contribution to the regional burden. New substances, for example, must be assessed for their impact following local emissions. In general their contribution to the larger environmental burden will be small until high annual tonnages are reached. Local exposure assessment As with organic compounds, the precise emissions will need to be identified and quantified for the whole life-cycle of the substance. Emission factors should initially be based on the substance being considered. It is important to know whether the substance is soluble in water, or can be transformed into a soluble form. Thus some knowledge of the chemistry of the particular substance and its interaction with the receiving media is important. Where the metal compound is soluble or can be transformed to a soluble form, the prediction of the environmental concentration, PEClocal, can be based on the relevant soluble metal ion. The behaviour of the substance in a wastewater treatment plant can be modelled using SimpleTreat, although measured Kp values will have to be used (Section 2.3.7 of main text). Since the actual bioavailability of the metal ion will be determined by the properties of the receiving media, such as the pH and water hardness, the precise physico-chemical characteristics of this receiving media must be defined. In general, it will be defined in a way which optimises the bioavailability of the toxic species. Speciation models exist which may be used to determine the soluble fraction. The partitioning behaviour of the substance to sludge/sediment/soil can be based on the appropriate Kp values for the soluble ion. In some cases, the metal compound will be only poorly soluble and sufficiently stable to not rapidly transform to a water soluble form. In these circumstances, the substance itself should be assessed taking into account its specific partitioning characteristics. For the aquatic environment, it can be assumed as a first estimate that the substance will dissolve up to its water solubility limit, and that this fraction will be the bioavailable form. Refinement of the assessment may take into account kinetics of the dissolution. Regional exposure assessment As for organic substances, all emissions from both point and diffuse sources are assumed to contribute to the regional concentration, PECregional. Because of the wide range of transformation processes and longer timescales involved, it is assumed that all the individual metal compounds are changed to the ionic species. Where possible, information on kinetics of transformation processes should be taken into account. As bioavailability is influenced by various physico-chemical characteristics of the environment it is important to define a 'standard environment', especially for a regional assessment. It is proposed that a regional assessment is carried out under conditions that optimise the bioavailability with respect to ranges for pH, water hardness etc that are found in the natural environment. This environment will probably differ for each metal assessed. Multimedia fate models can be used to assess exposure of man and ecosystems to metals on a regional scale. In applying multimedia fate models all emissions, including point sources, are assumed to be diffuse. Transport of metals between the aqueous phase and soil/sediment/suspended matter should be described on the basis of measured soil/water, sediment/water and suspended matter/water equilibrium partition coefficients (Kp), instead of using common mathematical relationships based on, for example, octanol-water partition coefficients, as is usually done for organic 303
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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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Page 328 and 329: APPENDIX XI Appendix XI Environment
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Page 336 and 337: APPENDIX XIV Taxonomic group No. of
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