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MARINE RISK ASSESSMENT assumption. In practice this information is often available for production and/or large processing sites. It may also be possible to assume the presence of connection to an STP for certain industry and/or use categories if appropriate justification about the general connection frequency to the STP for that specific industry is provided. For releases to municipal wastewater of substances that are used for private or public use (substances belonging to IC5 and IC6, Appendix I), however, it can be assumed that the degree of treatment in a biological STP corresponds to the inland scenario (see Section 2.3.7.1). For discharges to a coastal zone, local dilution will be greater than in a freshwater river. First, initial dilution may occur if the density between the effluent and the saline receiving medium differs (Lewis, 1997). The initial dilution factor is usually around 10. Further dilution due to currents can also be assumed, particularly if the point of release is subject to tidal influences. In the Baltic or the Mediterranean sea, where there are almost no tidal influences compared to the Atlantic Ocean or the North Sea, only initial dilution may occur on calm days, but normally, further dilution due to currents is probable. Dilution factors of more than 500 have been determined from model simulations (based on current measurements) in the North Sea, 200 m away from the discharge point (e.g. Pedersen et al., 1994). A dilution factor for discharges to a coastal zone of 100 may then tentatively be assumed, which seems to be representative of a realistic worst case. The same estimation method as for inland exposure assessment can then be used to obtain the local concentration in seawater (Clocalseawater, see Section 2.3.8.3, equations 45-49). In certain circumstances, it may be possible to identify specific emission points which would allow the use of more precise information regarding the available distribution and fate processes. Such “site-specific” assessments should only be used when it is known that all the emissions emanating from the particular point in the life-cycle, e.g. manufacture, arise from a limited number of specific and identifiable points. In these circumstances each specific point of release will need to be assessed individually. If it is not possible to make this judgement, then the default assumptions should be applied. In “site-specific” assessments, due account can be taken of the true dilution available to the given emission as well as the impact of degradation, volatilisation, etc. in the derivation of the PEC. Normally, only dilution and adsorption to suspended sediment need be considered but site-specific conditions may indicate that valid local distribution models can be used. For estuaries, which are influenced by currents and tidal movements, it is assumed as a first approach that they are covered by either the inland or the marine risk assessment. Thus, no specific assessment is proposed. Then, the local concentration in seawater can be obtained with: 142 Clocal seawater = ( 1+ Kp susp Clocaleff -6 • SUSPwater •10 ) • DILUTION (83)
Explanation of symbols MARINE RISK ASSESSMENT Clocaleff concentration of the substance in the STP effluent [mg . l -1 ] eq. (33) Kpsusp solids-water partitioning coefficient of suspended matter [l . kg -1 ] eq. (24) SUSPwater concentration of suspended matter in the seawater [mg . l -1 ] 15 DILUTION dilution factor [-] 100 Clocalseawater local concentration in seawater during emission episode [mg . l -1 ] Kpsusp is derived as for inland risk assessment. For a specific estimation of the partitioning behaviour of substances in saltwater environments see Section 4.2.2. It is recognised that the dilution available to a discharge will also be related to the actual volume of that discharge. In the freshwater scenario, this discharge volume is standardised to a volume of 2,000 m 3 /day ie. the outflow from a standard STP. It is therefore proposed that the discharge volume to the marine environment is also normalised at 2,000 m 3 /day such that the quantity of the substance discharged (in kg/day) is assumed, for modelling purposes, to be diluted into this volume prior to discharge. For indirect human exposure and secondary poisoning, an annual average concentration in surface water is calculated: Explanation of symbols = Clocal Clocal seawater, ann seawater • Temission 365 Clocalseawater local concentration in seawater during emission episode [mg . l -1 ] eq. (83) Temission number of days per year that the emission takes place [d . yr -1 ] App. IB Clocalseawater,ann annual average local concentration in seawater [mg . l -1 ] The concentration at the regional scale (PECregionalseawater) is used as background concentration for the local scale. Therefore, these concentrations are summed: Explanation of symbols (84) seawater = Clocal seawater + PECregional (85) PEClocal seawater seawater, ann= Clocal seawater, ann + PECregional (86) PEClocal seawater Clocalseawater local concentration in seawater during episode [mg . l -1 ] eq. (83) Clocalseawater,ann annual average concentration in seawater [mg . l -1 ] eq. (84) PECregionalseawater regional concentration in seawater [mg . l -1 ] 4.2.5 PEClocalseawater predicted environmental concentration during episode [mg . l -1 ] PEClocalseawater,ann annual average predicted environmental concentration [mg . l -1 ] If relevant site-specific information is available, it can be used to improve the assessment. Some significantly different exposure situations need to be reviewed though: 143
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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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Page 99 and 100: Output ENVIRONMENTAL EXPOSURE ASSES
Page 101 and 102: 3 EFFECTS ASSESSMENT 3.1 INTRODUCTI
Page 103 and 104: 3.2.1.1 Completeness of data New su
Page 105 and 106: EFFECTS ASSESSMENT • it is clearl
Page 107 and 108: EFFECTS ASSESSMENT 3.3 EFFECTS ASSE
Page 109 and 110: Table 16 Assessment factors to deri
Page 111 and 112: Input data EFFECTS ASSESSMENT The m
Page 113 and 114: Estimation of the PNEC The PNEC is
Page 115 and 116: EFFECTS ASSESSMENT biodegradability
Page 117 and 118: Table 17 Test systems for derivatio
Page 119 and 120: EFFECTS ASSESSMENT representative o
Page 121 and 122: In the partitioning method, it is a
Page 123 and 124: EFFECTS ASSESSMENT As mentioned in
Page 125 and 126: 3.6.2.1 Calculation of PNEC using t
Page 127 and 128: 3.7 EFFECTS ASSESSMENT FOR THE AIR
Page 129 and 130: EFFECTS ASSESSMENT procedure availa
Page 131 and 132: EFFECTS ASSESSMENT bioaccumulation
Page 133 and 134: EFFECTS ASSESSMENT For some chemica
Page 135 and 136: EFFECTS ASSESSMENT i.e. without enh
Page 137 and 138: Conversion factors for laboratory a
Page 139 and 140: EFFECTS ASSESSMENT • relative sen
Page 141 and 142: EFFECTS ASSESSMENT Earthworms are a
Page 143 and 144: MARINE RISK ASSESSMENT environment
Page 145 and 146: MARINE RISK ASSESSMENT of equal rel
Page 147 and 148: 4.2.3.3 Marine biodegradation simul
Page 149: MARINE RISK ASSESSMENT In addition
Page 153 and 154: MARINE RISK ASSESSMENT evaluate the
Page 155 and 156: MARINE RISK ASSESSMENT marine water
Page 157 and 158: MARINE RISK ASSESSMENT The addition
Page 159 and 160: MARINE RISK ASSESSMENT Statistical
Page 161 and 162: MARINE RISK ASSESSMENT sediment, fo
Page 163 and 164: Table 27 Assessment factors for der
Page 165 and 166: Table 28 continued Acute and chroni
Page 167 and 168: MARINE RISK ASSESSMENT of different
Page 169 and 170: MARINE RISK ASSESSMENT • a measur
Page 171 and 172: MARINE RISK ASSESSMENT b. the conce
Page 173 and 174: MARINE RISK ASSESSMENT mechanisms s
Page 175 and 176: MARINE RISK ASSESSMENT The use of t
Page 177 and 178: 4.4.4.2 Assessment of measured BCF
Page 179 and 180: MARINE RISK ASSESSMENT required to
Page 181 and 182: Table 33 Overview of PEC/PNEC ratio
Page 183 and 184: RISK CHARACTERISATION If a refineme
Page 185 and 186: Classified dangerous to the Environ
Page 187 and 188: RISK CHARACTERISATION eaters. This
Page 189 and 190: 6 TESTING STRATEGIES 6.1 INTRODUCTI
Page 191 and 192: TESTING STRATEGIES Performance of a
Page 193 and 194: TESTING STRATEGIES Care must be tak
Page 195 and 196: Algal testing Algae toxicity test (
Page 197 and 198: TESTING STRATEGIES • long-term te
Page 199 and 200: 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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APPENDIX I IC = 9: MINERAL OIL AND
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APPENDIX I IC = 11: POLYMERS INDUST
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APPENDIX I IC =13: TEXTILE PROCESSI
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APPENDIX I IC = 16: ENGINEERING IND
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APPENDIX I Appendix I-a: List of sy
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APPENDIX I No. Use Category No. Fun
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APPENDIX I Appendix I-b: List of sy
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APPENDIX I 290 Organic intermediate
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APPENDIX I Other IC/UC combinations
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APPENDIX II Appendix II Fate of che
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APPENDIX II b) Inherent biodegradab
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APPENDIX II log H % removal -4 -3 -
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APPENDIX III Appendix III Evaluatio
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APPENDIX III Field studies In gener
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APPENDIX IV together the mentioned
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290 Table 1 Selected soil test meth
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292 Table 1 continued Selected soil
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298 Table 1 Selected freshwater sed
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APPENDIX VII Appendix VII Toxicity
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APPENDIX VIII collection), and that
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APPENDIX VIII chemicals (see Sectio
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APPENDIX VIII Multimedia fate model
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APPENDIX VIII Monitoring data Metal
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APPENDIX VIII homeostatic regulatio
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APPENDIX IX based on the proportion
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APPENDIX IX Definition of “blocks
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APPENDIX IX these “blocks” will
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APPENDIX IX and PNECs for the “bl
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APPENDIX XI Appendix XI Environment
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APPENDIX XII Appendix XII Connectio
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APPENDIX XII +40% compared to 1992.
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APPENDIX XIII other substance is be
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APPENDIX XIV Taxonomic group No. of
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