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APPENDIX VIII Monitoring data Metals are a group of compounds for which relatively many reliable monitoring data in all environmental compartments are present. Given the fact that the group of metals is limited to a small number of compounds, for which usually sufficient monitoring data are available, risk assessment may well be based on monitoring data. In general monitoring data are preferred over model calculations. When interpreting the data, natural background concentrations, ambient background concentrations and availability for uptake by biota need to be taken into account. One should be aware that for the aquatic environment metal concentrations may sometimes be reported as dissolved concentrations and sometimes as total concentrations. Dissolved concentrations can be derived from total concentrations by means of the concentrations of dissolved organic matter and suspended particulate matter and partition coefficients between water and either organic or particulate matter. Since, as indicated before, risk assessment is to be performed on the basis of availability, dissolved concentrations should preferably be used since these indicate the bioavailable metal fraction in the aquatic environment. For soils and sediments sufficient information is only rarely available from monitoring data to directly determine the bioavailable metal fraction. By applying the appropriate Kp values, estimates of the available metal concentrations can be obtained. PECs from calculations and PECs from monitoring data can be compared. In cases where calculated PECs are below PECs based on measured concentrations, natural background and ambient background concentrations should be taken into consideration. Effects assessment Availability of data Toxicity data are available for most metals in sufficient quantity, since there are few compounds, and various toxicity data exist at least for the soluble metal salts. Most data are available for the toxic effects of metals on aquatic organisms, to a lesser extent data are present for terrestrial and sediment-dwelling organisms. Usually most data are based on total concentrations of the metals under investigation. For essential metals deficiency data must be taken into account. The data are available both on short and long-term tests, and are present for species from various trophic levels. These data can be used for the effect assessment in all compartments following the procedures for assessing the adequacy of data as presented in the main text (see Section 3.2). However, some metal-specific criteria must be taken into account: physico-chemical test conditions that define the metal speciation and bioavailability should be relevant for field conditions: water hardness, pH, alkalinity, presence of complexing agents (humic acids and EDTA); content of metal already present in the test medium, especially for soils taken from the field and natural waters. As metals are natural constituents of the biosphere these background concentrations can influence the test results. However, it should be noted that the bioavailability of the background concentration for soils is probably less than that of the “added” metal; for essential metals organisms of a given habitat are conditioned to the natural concentration range for essential elements. Within this range they can regulate their metal uptake in such a way that their internal concentration is kept relatively stable (homeostasis). This implies that organisms tested should originate and be cultivated within this optimal concentration range. 308
Derivation of the PNEC APPENDIX VIII PNECs can be derived through the application of assessment factors on the basis of the available data assessed according to the criteria given above. Standard methods applied elsewhere (e.g. for organic compounds) can be used for this (see Sections 3.3/3.7 of the main text). However, because of the specific mode of action that metals may have for some species, care should be taken in extrapolating short-term toxicity data to the PNEC using the standard assessment factors in Section 3.3. For many metals sufficient long-term toxicity data for aquatic organisms may be present to enable statistical extrapolation, results of which can support the results of PNECs calculated using assessment factors. Calculated PNECs derived for essential metals may not be lower than natural background concentrations. A prerequisite for the derivation of the PNEC is that it is done on the basis of the same level of availability as in exposure assessment: Results from aquatic toxicity tests are usually expressed as total concentrations. As a first approach total concentrations have to be recalculated to dissolved concentrations using partition coefficients. If this is not possible, the total concentration can be set equal to the dissolved concentration. Differences in test systems, e.g. (semi-)static versus continuous flow systems and natural versus standard water, have to be considered; For the terrestrial compartment many data exist, but most are only expressed as total concentration that has been added to the test media. This added amount will be partitioned among the aqueous and the solid phase. Application of partition coefficients to calculate the available concentration in soil can be applied. Soil type correction, using reference lines should be applied to correct for differences among soil types (see also Section 3.6.2 of the main text). In future risk assessment for the terrestrial compartment one should be aware of the different routes of exposure that exist among terrestrial species: for species that are not exposed through the aqueous phase, the (physico-chemically) available fraction needs not be correlated to the bioavailability; Some of the metals are essential metals, having a function in biological processes at low concentrations. Shortage of micronutrients may cause malfunction. This implies that in setting the PNEC information on deficiency levels should be taken into account. It should, however, be noted that often no information on deficiency levels of various metals for various species is available. Though some exceptions exist, in general ionic metal species are considered to be the dominant metal species taken up, and are thus considered to be the metal species responsible for the toxic effect. Data on the concentration of ionic species in aquatic and terrestrial systems are not readily available, and cannot, as yet, be applied on a regular basis in risk assessment. Bioaccumulation of essential metals Metals are taken up by organisms. For essential metals, biota regulate their uptake by means of the general physiological mechanism of homeostasis. By this mechanism, organisms will keep within a certain range of varying external concentrations, their intracellular levels relatively constant, in order to satisfy their requirements for that essential element. Homeostasis implies that organisms can deliberately concentrate essential elements if concentrations in the environment are very low. This may lead to high BCF values. On the other hand, the 309
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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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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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