Suomen ympäristökeskus

 

ISO 22032:2006 specifies a method for the determination of selected polybrominated diphenyl ethers (PBDE) in sediment and sludge using gas chromatography/mass spectrometry (GC-MS) in the electron impact (EI) or negative ion chemical ionization (NCI) mode. When using GC-EI-MS, the method is applicable to samples containing 0,05 to 25 micrograms per kilogram of tetra- to octabromo congeners and 0,3 to 100 micrograms per kilogram of decabromo diphenyl ether (BDE-209), respectively.

 

This document is applicable to lakes, which are water bodies occupying one or more basins with surface areas typically greater than 1 ha (0,01 km2) and maximum depths (at mean water level) greater than 1 m. All types of permanent and temporary lakes, including natural, modified and artificial, freshwater and brackish, except for those systems which regularly connect to the sea, are included in this document. Based on these criteria, it can be estimated that there are at least 500 000 natural lakes across Europe, most of which are located in the glaciated landscapes in northern and western provinces and in Scandinavia. Lakeland districts also occur locally in areas such as large river catchments (e.g. the Danubian plain) and around the Alps. Elsewhere, naturally occurring lakes are relatively sparse and in such areas reservoirs or pits are more common. This document is designed to: a) support environmental and conservation agencies in meeting the monitoring requirements of the WFD (Article 8, Annex II and Annex V); b) generate data sets appropriate for monitoring and reporting of Natura 2000 sites designated under the Habitats Directive and the Birds Directive; c) provide information supporting other environmental reporting requirements (e.g. in relation to biodiversity or environmental impact assessment); d) support lake management and restoration initiatives. This document: e) defines the key term of ‘hydromorphology’ and other terms relating to the morphological characteristics of lakes and their hydrological regimes; f) details essential features and processes of lakes that should be characterized as part of a hydromorphological survey and for determining the hydromorphological condition of a lake; g) identifies and defines the key pressures affecting European lakes; h) provides guidance on strategies for collecting hydromorphological data depending on resources available and the anticipated use of the assessment; a hierarchy of approaches is recognized from the ‘overview method’ utilizing existing databases, maps and remote sensing data through to recognized field-based survey techniques such as Lake Habitat Survey (LHS) [3]; i) offers guidance on data presentation; j) establishes guidance on data quality assurance issues. This document does not deal with biological assessments in lakes such as the presence or absence of individual species or community composition, nor does it attempt to link specific hydromorphological features with their associated biological communities or to create a classification based on such links. However, it is relevant where plants or other organisms form significant structural elements of the habitat (e.g. a gradation from riparian to littoral vegetation). With respect to the WFD, the hydromorphological condition of a lake only contributes to its status classification at high ecological status (HES). Hydromorphological conditions are not defined for good and moderate status but shall be sufficient to support the biological elements. However, some countries are now beginning to classify lakes according to their hydromorphology. The information gathered by using this standard can provide a basis for classification, but this classification is the subject of EN 16870 and not EN 16039.

 

ISO 19204:2017 describes in a general way the application of the soil quality TRIAD approach for the site-specific ecological risk assessment of contaminated soils. In detail, it presents in a transparent way three lines of evidence (chemistry, ecotoxicology and ecology) which together allow an efficient, ecologically robust but also practical risk assessment of contaminated soils. This procedure can also be applicable to other stress factors, such as acidification, soil compaction, salinization, loss of soil organic substance, and erosion. However, so far, no experience has been gained with these other applications. Therefore, this document focuses on soils contaminated by chemicals. NOTE 1 This document focuses on ecological risk assessment. Thus, it does not cover human health end points. In view of the nature of this document, the investigation procedure is described on a general level. It does not contain details of technical procedures for the actual assessment. However, this document includes references relating to technical standards (e.g. ISO 15799, ISO 17616) which are useful for the actual performance of the three lines of evidence. In ecological risk assessment, the effects of soil contamination on the ecosystem are related to the intended land use and the requirements that this use sets for properly functioning soil. This document describes the basic steps relating to a coherent tool for a site-specific risk assessment with opportunities to work out site-specific details. ISO 19204:2017 can also be used for the evaluation of clean-up operations, remediation processes or management measures (i.e. for the evaluation of the environmental quality after having performed such actions). NOTE 2 This document starts when it has already been decided that an ecological risk assessment at a given site needs to be performed. In other words, the practical performance of the soil quality TRIAD and the evaluation of the individual test results will be described. Thus, nothing will be said about decisions whether (and if yes, how) the results of the assessment are included in soil management measures or not. NOTE 3 The TRIAD approach can be used for different parts of the environment, but this document focuses mostly on the soil compartment. Comparable documents for other environmental compartments are intended to be prepared in addition (e.g. the terrestrial aboveground compartment) in order to perform a complete site assessment, based on the same principles and processes.

 

ISO 5667-15:2009 provides guidance on procedures for the preservation, handling and storage of samples of sewage and waterworks sludge, suspended matter, saltwater sediments and freshwater sediments, until chemical, physical, radiochemical and/or biological examination can be undertaken in the laboratory. The procedures in ISO 5667-15:2009 are only applicable to wet samples of sludge, sediment and suspended matter.

 

This document specifies the general requirements on procedures for the preservation, handling and storage of samples of sewage and waterworks sludge, suspended matter, marine sediments and freshwater sediments for either chemical, physical, radiochemical, hydrobiological or microbiological examination, or all, in the laboratory. The procedures in this document are not applicable to dried samples of sludge, sediment and suspended matter. NOTE The storage conditions given do not necessarily apply for derived samples, e.g. sediment eluates or extracts. This document is not applicable to samples intended for biotesting with ecotoxicological or biological assays (which is specified in ISO 5667-16[5]) nor intended for microplastics (which is specified in ISO 5667-27[7]).

 

This document describes in a general way the application of the soil quality TRIAD approach for the site-specific ecological risk assessment of contaminated soils. In detail, it presents in a transparent way three lines of evidence (chemistry, ecotoxicology and ecology) which together allow an efficient, ecologically robust but also practical risk assessment of contaminated soils. This procedure can also be applicable to other stress factors, such as acidification, soil compaction, salinization, loss of soil organic substance, and erosion. However, so far, no experience has been gained with these other applications. Therefore, this document focuses on soils contaminated by chemicals. NOTE 1 This document focuses on ecological risk assessment. Thus, it does not cover human health end points. In view of the nature of this document, the investigation procedure is described on a general level. It does not contain details of technical procedures for the actual assessment. However, this document includes references relating to technical standards (e.g. ISO 15799, ISO 17616) which are useful for the actual performance of the three lines of evidence. In ecological risk assessment, the effects of soil contamination on the ecosystem are related to the intended land use and the requirements that this use sets for properly functioning soil. This document describes the basic steps relating to a coherent tool for a site-specific risk assessment with opportunities to work out site-specific details. This document can also be used for the evaluation of clean-up operations, remediation processes or management measures (i.e. for the evaluation of the environmental quality after having performed such actions). NOTE 2 The application of this document starts when it has already been decided that an ecological risk assessment at a given site needs to be performed. In other words, the practical performance of the soil quality TRIAD and the evaluation of the individual test results will be described. Thus, nothing will be said about decisions whether (and if yes, how) the results of the assessment are included in soil management measures or not. NOTE 3 The TRIAD approach can be used for different parts of the environment, but this document focuses mostly on the soil compartment. Comparable documents for other environmental compartments are intended to be prepared in addition (e.g. the terrestrial aboveground compartment) in order to perform a complete site assessment, based on the same principles and processes.

 

This document specifies methods used to determine the concentration of plutonium and neptunium isotopes in water by inductively coupled plasma mass spectrometry (ICP-MS) (239Pu, 240Pu, 241Pu and 237Np). The concentrations obtained can be converted into activity concentrations of the different isotopes[9]. Due to its relatively short half-life and 238U isobaric interference, 238Pu can hardly be measured by this method. To quantify this isotope, other techniques can be used (ICP-MS with collision-reaction cell, ICP-MS/MS with collision-reaction cell or chemical separation). Alpha spectrometry measurement, as described in ISO 13167[10], is currently used[11]. This method is applicable to all types of water having a saline load less than 1 g·l-1. A dilution of the sample is possible to obtain a solution having a saline load and activity concentrations compatible with the preparation and the measurement assembly. A filtration at 0,45 µm is needed for determination of dissolved nuclides. Acidification and chemical separation of the sample are always needed. The limit of quantification depends on the chemical separation and the performance of the measurement device. This method covers the measurement of those isotopes in water in activity concentrations between around[12][13]: — 1 mBq·l-1 to 5 Bq·l-1 for 239Pu, 240Pu and 237Np; — 1 Bq·l-1 to 5 Bq·l-1 for 241Pu. In both cases, samples with higher activity concentrations than 5 Bq·l-1 can be measured if a dilution is performed before the chemical separation. It is possible to measure 241Pu following a pre-concentration step of at least 1 000.

 

This document describes a method to expose test organisms (amphipods), directly on the field by a caging methodology, with the aim to measure bioaccumulation of chemical substances on a monitoring station, i.e. either the concentrations of metals or organic compounds, or both, accumulated in the organisms. This document also describes the specifications for test organism selection and conditioning, in situ exposure, and finally sorting and conditioning of the surviving organisms after exposure. This document does not apply to organism preparation methods (freeze-drying, extraction, mineralization) and quantification of the chemical substances.

 

ISO 13196:2013 specifies the procedure for screening soils and soil-like materials for selected elements when handheld or portable energy-dispersive XRF spectrometers are used. This quick method is assumed to be applied on-site to obtain qualitative or semiquantitative data that assists decisions on further sampling strategy for assessing soil quality. The higher the efforts for pretreatment used on soil samples, the better the analytical results can be expected. ISO 13196:2013 does not explicitly specify elements for which it is applicable, since the applicability depends on the performance of the apparatus and the objective of the screening. The elements which can be determined are limited by the performance of the instruments used, the concentration of the element present in the soil, and the requirements of the investigation (e.g. guideline value). For Hg, Cd, Co, Mo, V and Sb, a majority of instruments are not sensitive enough to reach sufficiently low limits of quantification (LOQ) to meet the requirements (limit or threshold values) set in the ordinances of different countries. In this case, other methods need to be employed to measure these low concentrations. Usually, wet chemical methods are used, based on aqua regia extracts, in combination with optical or mass spectrometric (MS) methods like atomic absorption spectrometry (AAS), inductively coupled plasma/optical emission spectrometry (ICP/OES) or ICP/MS.

 

This document specifies the procedure for screening soils for selected elements using handheld or portable equipment for energy dispersive X-ray fluorescence spectrometry (ED-XRF). It covers the application of this screening method to obtain qualitative or semi-quantitative data to assist decisions on a sampling strategy for detailed assessment of soil quality employing laboratory analytical chemical methods. NOTE 1 Screening methods generally provide qualitative or semi-quantitative concentration values that are indicative of concentration values, although occasionally they can give quantitative results under specific or limited conditions. NOTE 2 The greater the effort applied to the pretreatment of soil samples, the better the analytical results that can be expected (see e.g. Reference [19]). This document does not explicitly specify elements for which it is applicable, since the applicability depends on the performance of the apparatus and the objective of the screening. The elements which can be determined are limited by the performance of the instrument used, the concentrations of particular elements present in the soil, and the requirements of the investigation in terms of the minimum concentrations of concern (e.g. guideline value). NOTE 3 The XRF measurements of As, Cd, Co, Cr, Cu, Hg, Mo, Ni, Pb, Sb, Sn, V and Zn were validated as described in Annex A. NOTE 4 Annex B provides examples of when screening with a handheld ED-XRF spectrometer and a portable ED-XRF spectrometer can be useful. This document does not provide guidance on how to use the equipment to provide quantitative data for use in detailed site assessments. This document does not cover how the results of multiple determinations are synthesized to address the objectives of an ED-XRF determination.

 

This document specifies a method for the measurement of 99Tc in all types of waters by liquid scintillation counting (LSC). The method is applicable to test samples of supply/drinking water, rainwater, surface and ground water, as well as cooling water, industrial water, domestic, and industrial wastewater after proper sampling and handling, and test sample preparation. A filtration of the test sample is necessary. The detection limit depends on the sample volume and the instrument used. The method described in this document, using currently available LSC instruments, has a detection limit of approximately 5 Bq·kg-1 to 20 Bq·kg-1, which is lower than the WHO criteria for safe consumption of drinking water (100 Bq l-1)[3]. These values can be achieved with a counting time of 30 min for a sample volume varying between 14 ml to 40 ml. The method presented in this document is not intended for the determination of ultra-trace amount of 99Tc. The activity concentration values in this document are expressed by sample mass unit instead of sample volume unit as it is usually the case in similar standards. The reason is that 99Tc is measured in various matrix types such as fresh water or sea water, which have significant differences in density. The activity concentration values can be easily converted to sample volume unit by measuring the sample volume. However, it increases the uncertainty on the activity concentration result. The method described in this document is applicable in the event of an emergency situation, but not if 99mTc is present at quantities that could cause interference and not if 99mTc is used as a recovery tracer. The analysis of Tc adsorbed to suspended matter is not covered by this method. It is the user's responsibility to ensure the validity of this test method for the water samples tested.

 

WARNING Persons using this document should be familiar with normal laboratory practices. This document does not purport to address all of the safety problems, if any, associated with its use. It is the responsibility of the user to establish appropriate safety and health practices and to determine the applicability of any other restrictions. IMPORTANT — It is absolutely essential that tests conducted according to this document be carried out by suitably trained staff. This document specifies methods to determine 99Tc by liquid scintillation counting (LSC) in water supplies, drinking water, rainwater, surface and ground water, marine water, as well as cooling water, industrial water, domestic, and industrial wastewater after proper sampling, handling, and test sample preparation. The detection limit depends on the sample volume, the instrument used, the background count rate, the detection efficiency, the counting time, and the chemical yield. The minimum detectable activity of the methods described in this document, using currently available LSC apparatus, is approximately 5 Bq·l-1 to 20 Bq·l-1, which is lower than the WHO criteria for safe consumption of drinking water (100 Bq·l-1).[4] These values can be achieved with a counting time of 60 min for a sample volume varying between 14 ml to 40 ml. The method presented in this document is not intended for the determination of ultra-trace activity concentrations of 99Tc. The method described in this document is applicable in the event of an emergency situation, but not if 99mTc is present at quantities that could cause interference and not if 99mTc is used as a recovery tracer. Filtration of the test sample is necessary for the methods described in this document if suspended solids are present as the methods presented in this document can only be used to determine soluble 99Tc. The analysis of 99Tc adsorbed to suspended matter is not covered by this method. The analysis of the insoluble fraction requires a mineralization step that is not covered by this document. In this case, the measurement is made on the different phases obtained. The final activity is the sum of all the measured activity concentrations. It is the user’s responsibility to ensure the validity of this test method for the water samples tested.