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MARINE RISK ASSESSMENT More details on the features of these models can be found in the section on calculation of PECregional for the freshwater environment (Section 2.3.8.7.) 6 . The calculation of PECregional according to this scenario provides the results for the generic risk assessment that is necessary for the risk evaluation for new and existing substances and biocides. Sufficient information on sources and emissions and site-specific information on the suspended matter concentration, the flow rate and the dispersion velocity may be available so the generic assessment can be made more site-specific by overriding some of the default parameters or even can be replaced by site-specific models. The dispersion velocity greatly affects all calculated concentrations, while in addition the suspended matter content further affects the dissolved concentration in seawater for chemicals with high log Kow. For the marine environment, models are available that can be used to assess the concentrations in certain specific compartments (bays, estuaries, regions) of the marine environment to which specific industrial sites discharge wastewater. 4.3 MARINE EFFECTS ASSESSMENT 4.3.1 Effects Assessment for the aquatic compartment 4.3.1.1 Introduction Historically, the patterns of chemical production and usage resulting from urban and industrial development have led to the freshwater environment being considered to be the hydrosphere most at risk from these substances. Consequently, most regulatory schemes for evaluating the hazards and risks posed by new and existing substances have focussed primarily on the protection of freshwater communities. As a result there is a considerable body of data on the ecotoxicity of chemical substances to freshwater organisms (ECETOC, 1994a) 7. Where there is a need to assess the potential impact of substances entering estuarine and marine waters, any hazard or risk assessment should ideally be based upon data generated using a range of ecologically relevant saltwater species (for example algae, invertebrates and fish). This is particularly important given the greater diversity of species (particularly invertebrates) present in 6 A default length:width ratio of the coastal marine compartment has been set at 4:1. Assuming that this reflects the plume shape in the generic assessment situation, this implies a ratio between the advective sea current along the coast and the dispersive transport velocity perpendicular to that. If, in addition to the compartment dimensions, a value is chosen for the sea current, the value of the lateral dispersion coefficient follows, or vice versa. If then a value for the freshwater discharge into the coastal marine compartment is set too, mixing of freshwater with coastal seawater is determined completely. In the generic regional model the river discharges approximately 1000 m 3 /s into the continental model. With the dimensions of the sea compartment set to 40,000 m . 10,000 m . 10 m, and a suggested default value for the sea current of 0.03 m/s, taking into account the necessary dispersion coefficient of 50 m 2 /s, the freshwater content of the sea water inside the selected box would become approximately 10%. It should be noted that river water plumes in coastal waters vary greatly with local conditions (river flow, sea current, tide, depth, etc.). Prediction of site-specific dilution of river water into coastal seawater requires sitespecific knowledge of flows and salinity distributions. Rhine and Meuse water (2,000 m 3 /s) are known to mix with a sea current of 0.035 m/s in the southern North Sea, yielding a very long-streched plume with approximately 20% river water in the first 10 km of the coast. A dispersion coefficient of 20 m 2 /s adequately describes this situation. The Amazon river is known for its great plume. 7 The ECETOC database consists of 2,203 entries on 361 chemicals, covering 121 species. Data on freshwater species accounted for 1862 entries (84.5%) while data for saltwater (estuarine/marine) species accounted for 341 entries (15.5%). 146
MARINE RISK ASSESSMENT marine waters, relative to freshwaters (cf. Appendix XIV). There are also circumstances, however, where the special conditions existing in a particular environment such as that existing in the Baltic Sea, give rise to a reduced or limited species diversity and/or specific stresses such as low or variable salinity. In such circumstances of low species diversity, adverse impacts in individual species can have devastating impacts on the specialised ecosystem. Thus, while high species diversity may lead to a wide sensitivity distribution, but also considerable functional overlap, low species diversity may result in a lower sensitivity distribution but increase the ecosystem function dependency on individual keystone species. In both cases, the effects assessment must use, where possible, data relevant to the environmental compartment that is considered. However, compared to the situation for freshwaters, there are relatively few data on the effects of chemical substances on estuarine and marine organisms. Therefore, in practice there will be situations where saltwater toxicity data are needed for hazard/risk assessments, but may not be available. In these situations it may be necessary to use freshwater data in lieu of data for estuarine/marine species (Schobben et al., 1994; Karman et al., 1998). In using data on freshwater species to characterise the risk in the marine waters, a clear understanding of the comparability of effects data generated on both types of species is necessary. Furthermore, there is some evidence, e.g. for some metals, that species living in brackish water are more susceptible because of the salinity (osmotic) stress they have to endure in contrast to those of the same species living in truly marine conditions. Under these circumstances the applicability of the toxicity data needs to be considered on a case-by-case basis. 4.3.1.2 Evaluation of data It has been recognised for many years that there is a wider diversity of taxonomic groups (particularly invertebrates) in saltwaters compared to freshwaters and that many groups are only found in marine waters (see Russell and Yonge, 1928; Tait, 1978). Moss (1988) stated that 56 phyla were present in marine waters compared to 41 in freshwaters. No phyla are confined to freshwaters only while 15 phyla are found only in marine waters. These differences are partly due to the fact that multicellular animals originated in the seas and they have been well populated since the earliest fossil records. Nevertheless, an important part of any evaluation of data must involve an assessment of the usefulness of the main body of freshwater ecotoxicity data in predicting effects in the marine environment. Where such data can be used, the focus of further investigation can concentrate on additional factors which specifically characterise the marine conditions. Studies conducted on the comparability of sensitivity of freshwater and marine species have been hampered by the low level of substances for which a comparable dataset has been available. Nevertheless where such data are available, it has tended to show that there is no systematic bias in sensitivity where comparable tests and endpoints are paired. A recent report which collated much of the available data confirmed these findings (ECETOC, 2000). Based on the currently available data, it can be concluded that: • overall, the data reviewed and current marine risk assessment practice suggest a reasonable correlation between the ecotoxicological responses of freshwater and saltwater biota - at least for the usual aquatic taxa (i.e., fish, crustacea, algae). No marked difference in sensitivity between freshwater and saltwater biota appears that systematically applies across all three trophic levels considered; 147
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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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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
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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 and 150: MARINE RISK ASSESSMENT In addition
Page 151 and 152: Explanation of symbols MARINE RISK
Page 153: MARINE RISK ASSESSMENT evaluate the
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
Page 201 and 202: TESTING STRATEGIES A soil bioassay
Page 203 and 204: 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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