Suomen ympäristökeskus

 

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 spectrophotometric determination of the pHT of sea water on the total hydrogen ion concentration pH scale. The total hydrogen ion concentration, [H+]t, is expressed as moles per kilogram of sea water. The method is suitable for assaying oceanic levels of pHT from 7,4 to 8,2 for normal sea water of practical salinity ranging from 20 to 40.

 

This document specifies procedures for sampling, capture and preservation of environmental DNA (eDNA) in aquatic environments, stemming from organisms that are or have recently been present in a waterbody, have visited it or whose DNA has been introduced to the waterbody through some mechanism. This document also covers procedures for avoiding sample contamination and ensuring DNA quality, key properties of the filtering procedure and equipment and reporting standards. This document does not include the collection of eDNA from biofilms, sediments or similar sample types and does not cover sampling designs.

 

This document specifies procedures for sampling, capture and preservation of environmental DNA (eDNA) in aquatic environments, stemming from organisms — that are or have recently been present in a water body, or — whose DNA has been introduced to the water body through some mechanism. This document also specifies procedures for avoiding sample contamination and ensuring environmental DNA integrity during water filtration and sample preservation. It also specifies the required equipment and metadata reporting. This document excludes: — methods for the collection of eDNA from biofilms, sediments or similar sample types; — passive sampling methods; — sampling designs.

 

This document specifies a method for sampling and handling earthworms from field soils as a prerequisite for using these animals as bioindicators (e.g. to assess the quality of a soil as a habitat for organisms). This document applies to all terrestrial biotopes in which earthworms occur. The sampling design of field studies in general is given in ISO 18400-101 and guidance on the determination of effects of pollutants on earthworms in field situations is given in ISO 11268-3. These aspects can vary according to the national requirements or the climatic/regional conditions of the site to be sampled (see also Annex C). This document is not applicable for semi-terrestrial soils and it can be difficult to use under extreme climatic or geographical conditions (e.g. in high mountains). Methods for some other soil organism groups, such as collembolans, are covered in other parts of ISO 23611.

 

This document specifies a method for sampling and handling earthworms from field soils as a prerequisite for using these animals as bioindicators (e.g. to assess the quality of a soil as a habitat for organisms). This document is applicable to all terrestrial biotopes in which earthworms occur. This document does not apply to semi-terrestrial soils (i.e. soils that are partly aquatic, such as bogs, beaches, marshes, stream margins) and it can be difficult to use under extreme climatic or geographical conditions (e.g. in high mountains). Methods for other soil organism groups, such as micro-arthropods and enchytraeids (mesofauna), are covered in other parts of the ISO 23611 series.

 

This document provides requirements and recommendations for the design of field studies with soil invertebrates (e.g. for the monitoring of the quality of a soil as a habitat for organisms). It applies to all terrestrial biotopes inhabited by soil invertebrates, although this information can vary according to the national requirements or the climatic and regional conditions of the site to be sampled. NOTE While this document aims to be applicable globally, the existing information refers mostly to temperate regions. However, the (few) studies from other (tropical and boreal) regions, as well as theoretical considerations, allow the conclusion that the principles laid down in this document are generally valid.[1],[11],[12],[13]

 

This part of ISO 23611 provides guidance for the design of field studies with soil invertebrates (e.g. for the monitoring of the quality of a soil as a habitat for organisms). Detailed information on the sampling of the most important soil organisms is provided in the other parts of this International Standard (ISO 23611-1 to ISO 23611-5). This part of ISO 23611 is used for all terrestrial biotopes in which soil invertebrates occur. Basic information on the design of field studies in general is already laid down in ISO 10381-1. This information can vary according to the national requirements or the climatic/regional conditions of the site to be sampled. NOTE While this part of ISO 23611 aims to be applicable globally for all terrestrial sites that are inhabited by soil invertebrates, the existing information refers mostly to temperate regions. However, the (few) studies from other (tropical and boreal) regions, as well as theoretical considerations, allow the conclusion that the principles laid down in this part of ISO 23611 are generally valid, References [4], [6], [40], [21]. This part of ISO 23611 gives information on site-specific risk assessment of contaminated land, study of potential side effects of anthropogenic impacts (e.g. the application of chemicals or the building of roads), the biological classification and assessment of soils in order to determine the biological quality of soils, and longterm biogeographical monitoring in the context of nature protection or restoration, including global change (e.g. as in long-term ecological research projects).

 

This document describes a method for the determination of the acute toxicity to one of three specified species of marine copepod (Copepoda, Crustacea). This document is applicable to: a) industrial or sewage effluents, treated or untreated, after decantation, filtration or centrifugation if necessary; b) marine or estuarine waters; c) aqueous extracts (pore water, elutriates, eluates and leachates) from sediments; d) chemical substances which are soluble, or which can be maintained as a stable suspension or dispersion, under the conditions of the test.

 

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.

 

ISO 9308-2:2012 specifies a method for the enumeration of E. coli and coliform bacteria in water. The method is based on the growth of target organisms in a liquid medium and calculation of the "Most Probable Number" (MPN) of organisms by reference to MPN tables. This method can be applied to all types of water, including those containing an appreciable amount of suspended matter and high background counts of heterotrophic bacteria. However it must not be used for the enumeration of coliform bacteria in marine water. When using for the enumeration of E. coli in marine waters, a 1?10 dilution in sterile water is typically required, although the method has been shown to work well with some marine waters that have a lower than normal concentration of salts. In the absence of data to support the use of the method without dilution, a 1?10 dilution is used. This method relies upon the detection of E. coli based upon expression of the enzyme b-D-glucuronidase and consequently does not detect many of the enterohaemorhagic strains of E. coli, which do not typically express this enzyme. Additionally, there are a small number of other E. coli strains that do not express b-D-glucuronidase. The choice of tests used in the detection and confirmation of the coliform group of bacteria, including E. coli, can be regarded as part of a continuous sequence. The extent of confirmation with a particular sample depends partly on the nature of the water and partly on the reasons for the examination. The test described in ISO 9308-2:2012 provides a confirmed result with no requirement for further confirmation of positive wells.

 

This document specifies a method for the enumeration of E. coli and coliform bacteria in water. The method is based on the growth of target organisms in a liquid medium and calculation of the “Most Probable Number” (MPN) of organisms by reference to MPN tables or by use of appropriate formulae 1]. This method can be applied to a range of types of water (for example drinking water, groundwater, surface water, recreational water and wastewater),[2-5] including those containing a considerable amount of suspended matter and high background counts of heterotrophic bacteria. Users should satisfy themselves that any product used has been validated for its intended use (e.g. chlorinated drinking water) and should generate performance characteristics using ISO13843.[6] Performance characteristic data generated prior to 2017 using ISO TR 13843[7] is also acceptable. If a water sample has some background colour, the incubated sample should be compared to a blank control of the same water sample This method relies upon the detection of E. coli based upon expression of the enzyme ß-D-glucuronidase and consequently does not detect some enteropathogenic strains of E. coli, which do not typically express this enzyme. Additionally, there are a small number of other E. coli strains that do not express ß-D-glucuronidase. As they are ß-D-galactosidase positive, they will appear as coliform bacteria.

 

ISO 13164-1:2013 gives general guidelines for sampling, packaging, and transporting of all kinds of water samples, for the measurement of the activity concentration of radon-222. The test methods fall into two categories: a) direct measurement of the water sample without any transfer of phase (see ISO 13164-2); b) indirect measurement involving the transfer of the radon-222 from the aqueous phase to another phase (see ISO 13164-3). The test methods can be applied either in the laboratory or on site. The laboratory is responsible for ensuring the suitability of the test method for the water samples tested.

 

ISO 13164-3:2013 specifies a test method for the determination of radon-222 activity concentration in a sample of water following its transfer from the aqueous phase to the air phase by degassing and its detection. It gives recommendations for rapid measurements performed within less than 1 h. The radon-222 activity concentrations, which can be measured by this test method utilizing currently available instruments, range from 0,1 Bq l-1 to several hundred thousand becquerels per litre for a 100 ml test sample. This test method is used successfully with drinking water samples. The laboratory is responsible for ensuring the validity of this test method for water samples of untested matrices. This test method can be applied on field sites or in the laboratory. Annexes A and B give indications on the necessary counting conditions to meet the required sensitivity for drinking water monitoring

 

This part of ISO 13164 specifies a test method for the determination of 222Rn activity concentration in a sample of water following its transfer from the aqueous phase to the gas phase by degassing and its detection. It gives recommendations for rapid measurements performed within less than 1 h. The 222Rn activity concentrations, which can be measured by this test method utilizing currently available instruments, range from 0,1 Bq·l-1 to several hundred thousand becquerels per litre for a 100 ml test sample. This test method is used successfully with drinking water samples. The laboratory is responsible for ensuring the validity of this test method for water samples of untested matrices. This test method can be applied on field sites or in the laboratory.

 

This part of ISO 13164 gives general guidelines for sampling, packaging, and transporting of all kinds of water samples, for the measurement of the activity concentration of 222Rn. The test methods fall into two categories: a) direct measurement of the water sample without any transfer of phase (see ISO 13164-2[7]); b) indirect measurement involving the transfer of the 222Rn from the aqueous phase to another phase (see ISO 13164-3[8] and 13164-4[9]). The test methods can be applied either in the laboratory or on-site. The laboratory is responsible for ensuring the suitability of the test method for the water samples tested.