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ENVIRONMENTAL EXPOSURE ASSESSMENT enhance their removal from the water phase by “stripping” them from the solid/liquid phases to the atmosphere. Substances may be removed from exhaust gaseous streams by scrubbing e.g. by adsorption on a suitable material or by passing through a trapping solution. Wastewater treatment One of the critical questions to answer in determining the PEC for the aquatic environment is whether or not the substance will pass through a wastewater treatment plant and if yes, through which kind of treatment plant before being discharged into the environment. The situation in the Member States concerning percentage connection to sewage works is quite diverse (see Appendix XII). The percentage connection rate across the Community is subject to improvement due to the implementation of the Urban Waste Water Treatment Directive (UWWTD, 91/271/EEC). This directive requires Member States (via transposition into national legislation) to ensure that wastewater from all agglomerations of > 2,000 population equivalents is collected and treated minimally by secondary treatment. The time limit for implementation of the directive is 31/12/98, 31/12/2000 or 31/12/2005 dependent on the size of the agglomeration and the sensitivity of the receiving water body. An interim figure of 80% connection to wastewater treatment is proposed for the regional standard environment. This value is thought to be representative for the actual situation in large urban areas at the time of revision of the TGD. Article 6 of the UWWTD allows Member States to declare non sensitive areas for which discharged wastewater from agglomerations between 10,000 and 150,000 population equivalents, which are located at the sea and from agglomerations between 2,000 and 10,000 population equivalents located at estuaries does not have to be treated biologically but only mechanically (primary treatment). It is notable that 4 Member States have applied this article, corresponding to < 9% of the organic load (in terms of population equivalents). The situation with respect to wastewater treatment at industrial installations is less clear. It may be assumed that many of the larger industrial installations are either connected to a municipal wastewater treatment plant or have treatment facilities on site. In many cases, these treatment plants are not biological treatment plants but often physico-chemical treatment plants in which organic matter is flocculated by auxiliary agents e.g. by iron salts followed by a sedimentation process resulting in a reduction of organic matter measured as COD of about 25-50%. In the present document, the above-described situation is taken into account as follows: • on a local scale, it is assumed that wastewater will pass through a STP before being discharged into the environment. Nevertheless, for the largest PEClocal in surface water, it is necessary to determine an aquatic PEClocal assuming that no sewage treatment will take place. This value should be determined in addition to the normal PEC that assumes sewage treatment to flag for possible local problems (this PEC/PNEC ratio will not normally be used in risk characterisation). The alternative/additional PEC can be used to explore the possibility of environmental impact in regions or industrial sectors where percentage connection to sewage works is currently low, so as to give indications to local authorities for needs of possible local risk reductions. The PEC without considering a STP-treatment will not be used in the exposure assessment, unless the substance considered has a specific use category where direct discharge to water is widely practised; • for a standard regional scale environment (definition see Section 2.3.8.1) it is assumed that 80% of the wastewater is treated in a biological STP and the remaining 20% released directly into surface waters (although mechanical treatment has some effect on eliminating organic matter, this is neglected because on the other hand stormwater overflows usually result in direct discharges to surface water even in the case of biological treatment. It is 58
ENVIRONMENTAL EXPOSURE ASSESSMENT assumed that these two adverse effects compensate each other more or less with regard to the pollution of the environment). The degree of removal in a wastewater treatment plant is determined by the physico-chemical and biological properties of the substance (biodegradation, adsorption onto sludge, sedimentation of insoluble material, volatilisation) and the operating conditions of the plant. As the type and amount of data available on degree of removal may vary, the following order of preference should be considered: Measured data in full scale STP The percentage removal should preferably be based upon measured influent and effluent concentrations. As with measured data from the environment, the measured data from STPs should be assessed with respect to their adequacy and representativeness. Consideration must be given to the fact that the effectiveness of elimination in treatment plants is quite variable and depends on operational conditions, such as retention time in the aeration tank, aeration intensity, influent concentration, age and adaptation of sludge, extent of utilisation, rainwater retention capacity, etc. The data may be used provided that certain minimum criteria have been met, e.g. the measurements have been carried out over a longer period of time. Furthermore, consideration should be given to the fact that removal may be due to stripping or adsorption (not degradation). In case no mass balance study has been performed, the percentage of transport to air or sludge should be estimated, e.g. by scaling the fractions to air and sludge from the tables in Appendix II to the measured removal. Data from dedicated STPs should be used with caution. For example, when measured data are available for highly adapted STPs on sites producing high volume site-limited intermediates, these data should only be used for the assessment of this specific use category of the substance. Simulation test data Simulation testing is the examination of the potential of a substance to biodegrade in a laboratory system designated to represent either the activated sludge-based aerobic treatment stage of a wastewater treatment plant or other environmental situations, for example a river. The wastewater treatment process can be studied in the laboratory by, e.g., the updated OECD guideline on simulation testing of aerobic sewage treatment (OECD, 2001b) or the older Coupled Units Test (OECD, 1981b). Removability is determined by monitoring the changes in DOC (Dissolved Organic Carbon) and/or COD (Chemical Oxygen Demand). A number of guidelines have recently been prepared, e.g. ISO/DIS 14952-1, draft OECD (2001d), OECD 307 (soil, 2000b), draft EU Annex V C.23, OECD 308 (sediment, 2000c), draft EU Annex V C.24. The Coupled Units Test is not suitable for adsorptive, poorly water-soluble and volatile substances because it is an open test and is only based on DOC analysis. Since, in addition, it is possible that adsorptive or volatile metabolites may be formed during biological degradation, this test cannot differentiate between biological degradation and other elimination processes. Investigations with a closed vessel version of the Coupled Units Test using radioactively labelled substances have been performed which would allow a determination of the complete mass balance and would also be suitable for volatile or adsorptive substances. However, there is no international standard method available for this modified test. There is insufficient information available on the applicability of elimination data from the laboratory test to the processes of a real sewage plant. The results can be extrapolated to 59
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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
Page 15 and 16: 1 GENERAL INTRODUCTION 1.1 BACKGROU
Page 17 and 18: GENERAL INTRODUCTION countries in t
Page 19 and 20: GENERAL INTRODUCTION PNEC is regard
Page 21 and 22: 2 ENVIRONMENTAL EXPOSURE ASSESSMENT
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Page 25 and 26: 2.2 MEASURED DATA ENVIRONMENTAL EXP
Page 27 and 28: ENVIRONMENTAL EXPOSURE ASSESSMENT w
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Page 31 and 32: ENVIRONMENTAL EXPOSURE ASSESSMENT T
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Page 35 and 36: Production ENVIRONMENTAL EXPOSURE A
Page 37 and 38: Back to processing Product at end o
Page 41 and 42: ENVIRONMENTAL EXPOSURE ASSESSMENT s
Page 43 and 44: Explanation of symbols ENVIRONMENTA
Page 45 and 46: ENVIRONMENTAL EXPOSURE ASSESSMENT s
Page 47 and 48: ENVIRONMENTAL EXPOSURE ASSESSMENT U
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Page 61 and 62: constant of zero. However, if it ca
Page 63 and 64: ENVIRONMENTAL EXPOSURE ASSESSMENT A
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Page 69 and 70: Primary Settler Aeration Tank 2 5 3
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Page 79 and 80: Table 10 Overview of different expo
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Page 83 and 84: 2.3.8.3 Calculation of PEClocal for
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Page 87 and 88: Guidance for calculating PEClocal i
Page 89 and 90: Concentration (% of initial) 160 14
Page 93 and 94: Calculation of PEClocalsoil For soi
Page 95 and 96: ENVIRONMENTAL EXPOSURE ASSESSMENT
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
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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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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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