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MARINE RISK ASSESSMENT waters, and may accumulate in sediments over time. In general substances with a Koc < 500 – 1000 L/kg are not likely sorbed to sediment (SETAC, 1993). To avoid extensive testing of chemicals a log Koc or log Kow of ≥ 3 can be used as a trigger value for sediment effects assessment. For most existing chemicals the number of toxicity data on infaunal and epibenthic organisms will be limited. As a screening approach the equilibrium method can be used to compensate for the lack of toxicity data if a PECmarine sediment can be determined on the basis of a measured concentration of the substance in water that is independent of the value of the Koc. If the PEC/PNEC determined using this method is > 1 then the need for testing with benthic organisms using spiked sediment should be considered. It is not necessary to apply the equilibrium partitioning method to predicted environmental concentrations obtained from application of an exposure model when such a model will have used the same Koc or log Kow value as that used to predict the PNECsediment. The reason is that the resulting PEC/PNEC ratio for sediment will have the same value as for the water compartment. In this case no quantitative risk characterisation for marine sediment should be performed. Under these circumstances the assessment conducted for the aquatic compartment will also cover the sediment compartment for chemicals with a log Kow up to 5. For substances with a log Kow > 5 (or with a corresponding Koc), however, the PEC/PNEC ratio for the aquatic compartment is increased by a factor of 10. The increased factor is justified by the fact that the equilibrium partitioning method considers mainly the exposure via the water phase and does not include that potential additional accumulation via sediment ingestion may occur for certain types of sediment dwelling invertebrates (see Section 8.2.3). Four situations can be distinguished for deriving a PNECsediment: 1. where only results from acute tests with benthic freshwater organisms are available (at least one) the risk assessment is performed both on basis of the tests and on the basis of the equilibrium partitioning method. The lowest PNECmarine sediment is then used for the risk characterisation. 2. where, in addition to the tests with freshwater benthic organisms, an acute toxicity test is performed with a marine benthic organism that is preferably representative of the same taxon that is judged to be the most sensitive in the freshwater tests. Under these circumstances an assessment factor of 1000 is applicable. A reduction of the assessment factor is only justified if sufficient long-term tests with sediment-dwelling organisms are available, and, if possible, where other evidence indicates that these tests include sensitive taxonomic groups. Also in this case a comparison with the screening approach has to be made and the lowest PNECsediment should be used for the risk characterisation. 3. where long-term toxicity data are available for benthic freshwater organisms. Under this circumstance the PNECmarine sediment is calculated using assessment factors for long-term tests. This approach is explained in Section 4.3.2.4. 4. where long-term toxicity data are available for benthic freshwater and a minimum of two marine organisms. Under these circumstances a PNECmarine sediment is calculated using the lower assessment factors that are associated with data obtained from long-term tests. A PNECmarine sediment obtained from such data is preferred for risk assessment. This approach is explained in Section 4.3.2.4. Table 18 in Section 3.5.2 presents an overview of different data configurations and explains how to use them for the risk characterisation for sediment. Attention should be paid to the fact that very often contaminants are not analysed in whole sediment but in a certain fraction of the 152
MARINE RISK ASSESSMENT sediment, for example in the sediment fraction of particles < 63 µm. The organic carbon content of this fraction is typically 15-30% for marine sediment while for whole marine sediments it is generally less than 2%. It is important, for reasons of comparability of PEC and PNEC values, that the organic carbon content of sediment used for toxicity tests are comparable with those of actual marine sediments. If not there are likely to be concerns regarding the relative bioavailability of a substance in the different sediments. 4.3.2.3 Calculations of PNEC for marine sediment using the equilibrium method In the absence of any ecotoxicological data for sediment-dwelling organisms, but with measured data to predict the PECmarine sediment, the PNECmarine sediment may provisionally be calculated using the equilibrium partitioning method. This method uses the PNECsaltwater for aquatic organisms and the marine suspended matter/water partitioning coefficient. The assumptions that are made in this method are described in Section 3.5.3. Based on the equilibrium partitioning the following equation is applied: Explanation of symbols K susp−water PNEC marine−se dim ent = ⋅ PNECsaltwater ⋅1000 (88) RHO susp PNECsaltwater Predicted No Effect Concentration in saltwater [mg . l -1 ] RHOsusp bulk density of suspended matter [kg . m -3 ] eq. (18) Ksusp water partition coefficient suspended matter water [m 3. m -3 ] eq. (24) PNECmarine sediment Predicted No Effect Concentration in marine sediment [mg . kg -1 ] In Section 3.5.2 a remark is made with respect to the calculation of PNECmarine sediment using the equilibrium partitioning method. The equilibrium partitioning method considers uptake via the water phase, while uptake may also occur via other exposure pathways such as ingestion of sediment or direct contact with sediment. This may be important, especially for chemicals that have a tendency to adsorb to sediment organic matter, for example those with a log Kow greater than 3. Direct uptake from marine sediment is also observed in studies with marine benthic organisms and may significantly contribute to the uptake of organic contaminants such as PAHs (Kaag, 1998). There is also however evidence from studies in soil and in marine sediment that the proportion of the total dose taken up through intake of sediment particles remains low for chemicals with a log Kow up to 5. From other studies it is obvious that feeding mode also influences uptake of substances (via water or ingestion of sediment). Furthermore the absorption of contaminants in the gastrointestinal tract has been found to be increased compared with absorption from the surrounding water (Mayer et al., 1996; Voparil and Mayer, 2000). However, no quantitative conclusions can be drawn from these studies regarding uptake of substances from sediment. For substances with a log Kow greater than 5 (or with a corresponding Kpsed) the equilibrium partitioning method is used in a modified way in order to take account of possible uptake via ingestion of sediment. Thus the resulting PEC/PNEC ratio is increased by a factor of 10 for these compounds. It should be borne in mind that this approach is considered as a screening level assessment of the risk to sediment dwelling organisms. If with this method a PEC/PNEC ratio > 1 is derived then tests, preferably long-term, with benthic organisms using spiked sediment have 153
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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
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 and 150: MARINE RISK ASSESSMENT In addition
Page 151 and 152: Explanation of symbols MARINE RISK
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: MARINE RISK ASSESSMENT Statistical
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
Page 205 and 206: REFERENCES IPCS (2000). Framework f
Page 207 and 208: REFERENCES OECD (1984f). Activated
Page 209 and 210: 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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