Soils are one of the world's hotspots for biodiversity (Parker, 2010). Biota – both micro- and macro-organisms – in soil form strong networks and complex food webs, which determine the efficacy of the soil ecosystem functions (e.g. nutrient cycling, C storage and turnover, water retention, and modulation of soil structure) (Creamer et al., 2016). These functions support a range of ecosystem services that are indispensable for soil use in agriculture, horticulture, or silviculture (Nannipieri et al., 2017). At the same time, soil biota are strongly impacted by various anthropogenic activities, including ongoing global and climate change, pollution, as well as degradation and destruction of the terrestrial environment (Gomiero, 2016; Montgomery, 2008; Wagg et al., 2014). Consequently, investigations of the soil biome structure and function became an emerging topic in soil and environmental sciences (Griffiths and Philippot, 2013). As such, the number of studies describing the ecology of soils and ecosystem functioning has increased significantly over the past few decades and has resulted in the development of new methods for the assessment of microbial communities (e.g. Guillaume et al., 2016; Tian et al., 2018). In comparison, the ecotoxicological assessment of human impacts (e.g. chemical pollution and mechanical compaction) using single-species tests, which are well-established methods, has remained constant (Brookes, 1995; Joergensen and Emmerling, 2006).

Characterising the natural state of a soil's biome is a quite challenging task. In addition to its huge structural and functional diversity, soil biomes are influenced by strong temporal dynamics including seasonal weather conditions and the enormous spatial heterogeneity, which ranges from field scale to microscale (Kuffner et al., 2012; Regan et al., 2014; Suriyavirun et al., 2019). All of these intrinsic properties hinder the interpretation of data obtained from the analysis of soil biomes and the measurement of their functional traits.

Despite the fundamental methodological advances over the past years, which allow for an in-depth analysis of microbiomes and, to some extent, other soil-living organisms (e.g. Joergensen and Emmerling, 2006; Paul, 2015; Yates et al., 2016), only a limited number of soil biological methods have been standardised (for details, see Sect. 3). As a result, large and often significant deviations are observed in the results obtained when non-standardised methods are used (e.g. Strickland and Rousk, 2010). This is especially true for methods that are based on high throughput sequencing approaches, where variability and bias in data can occur from the “wet-lab” steps right through the various bioinformatics pipeline analysis steps (Quince et al., 2017). Therefore, the comparability between datasets generated by different laboratories using different methods or modified protocols of the same method is problematic. Consequently, the development of quality indices and threshold values, respectively, for assessing soil quality is nearly impossible (Bastida et al., 2008). Presumably, this is why the number of meta-analyses in soil biology remains small.

Given that there is a lack of harmonisation between existing methods and, at the same time, a proliferation of new methods, there is a need to identify the most promising methods described in the literature that can be standardised to produce reliable indicators for soil quality (e.g. Philippot et al., 2012). At the Annual International Organization for Standardization (ISO) meeting of TC 190 (Soil Quality) in Fukuoka, Japan, in October 2013, a decision was made to compile a list of available methods and to identify those that would be suitable for assessing soil quality. Additionally, during a subsequent meeting of ISO TC 190/SC 4/WG 4 (Microbiological Methods) held in Paris, France, in March 2014, further discussions focused on the criteria for suitable methods to be comprised of microbial functional indicators. In this paper, we summarise the major outcomes of the discussions which took place over the past several years within ISO TC 190/SC 4. Therefore, besides collating a list of criteria for the selection of test methods for the future analysis of microbial functions in soil, the aim of this paper is to present our opinion, as members of the ISO TC 190 committee, to initiate further discussion on possible methods that should be standardised for future soil quality assessments.

Several papers addressing the task of identifying suitable methods to be used as biotic indicators (usually including faunal indicators) were published in the last few years, mainly in the context of EU research projects (e.g. Bispo et al., 2009; Faber et al., 2013; Ritz et al., 2009; Römbke et al., 2010). Here, we propose to base the selection of soil quality methods more on the “Ecosystem Service Approach” (MEA, 2005) which is increasingly recognised by both environmental scientists and regulatory agencies (Breure et al., 2012; Galic et al., 2012) and which takes into account that soils have been raised to the rank of a natural resource to be protected. As a consequence, and in addition to method development and application (including the assessment of biodiversity as a prerequisite for soil function), the focus of future activities should be the determination of soil microbial functions as recommended endpoints (Kvas et al., 2017; Nienstedt et al., 2012; van der Putten et al., 2010; TEEB, 2010). Consequently, we propose to assess both existing and new methods for the selection of microbial functional tests that support various soil ecosystem services. This structures our approach, simplifies the identification of ecologically relevant methods, and presumably increases their acceptance by users, including the regulatory and stakeholder community. The following soil functions and ecosystem services have been defined and are proposed to be used as a starting point for the development of future methods (MEA, 2005; Ockleford et al., 2017):

biodiversity, genetic resources, cultural services;

To assess possible methods, a list of criteria was used based on the “logical sieve” approach (Ritz et al., 2009). The list of criteria for the identification of functional indicators and associated methodologies (Table 1) was an outcome of the EU FP7 EcoFINDERS project (Faber et al., 2013). The criteria were compiled after sending a questionnaire to 25 partner institutions primarily working in the field of environmental science, mainly representing academia but also regulators and subcontracting laboratories. These criteria are applicable for different kinds of indicators and methods, including those addressing the functions of soil microbial communities. In the following sections, we assume that existing ISO standardised methods partly already fulfil these criteria, but not all relevant endpoints can be measured.

Current methods that have already been implemented as ISO standards are found in Table 2, whereas methods that might be considered for future standardisation are in Table 3. The compilation in Table 2 comprises methods to quantify microbial biomass (e.g. through fumigation extraction of microbial biomass carbon (MBC) and DNA) (Function 6) as well as for (further) analysis of structural microbial diversity (e.g. determination of microbial fingerprints by phospholipid fatty acids (PLFA) analysis) (Function 1). Additionally, microbial biomass, measured as respiratory activity, has been included in Table 2 but is not directly linked to one of the ecosystem services, as it provides important information on the activity of the complete microbiome (i.e. microflora and microfauna). Soil basal respiration normalised to MBC (ISO 14240-1, 1997; ISO 14240-2, 1997, Table 2) yields the metabolic quotient qCO2, which is a sensitive indicator for microbial carbon use efficiency (Anderson and Domsch, 1993). However, its use as an endpoint to assess anthropogenic and natural impacts on the soil microbiome has been controversially discussed in the literature (Wardle and Ghani, 1995). The microbial quotient (MBC related to the organic carbon content of a soil) is an indicator revealing changes in the microbial dynamic equilibrium of soils in response to exposure to natural or anthropogenic stressors (Pankhurst et al., 2001).

The biodiversity function (Function 1) addresses parameters related to the structural diversity of the soil microbiome. Here, respective ISO guidelines analysing PLFA, phospholipid ether lipids (PLEL) (ISO/TS 29843-1, 2010; ISO/TS 29843-2, 2011), and DNA (ISO 11063, 2012; ISO 17601, 2016) have already been well implemented into guidelines (Table 2). In addition, high throughput sequencing of barcodes of the ribosomal operon (16S rRNA gene for bacteria and archaea and ITS (internal transcribed spacer) region for fungi) has generated a large amount of data (Schöler et al., 2017). These approaches have also been used successfully for other microbial groups like protists (using the 18S rRNA gene as a target). As it is well accepted that the use of different primer pairs introduces different biases (Ramirez et al., 2018), standards have been recommended by international initiatives. For example, the Earth Microbiome project (http://www.earthmicrobiome.org, last access: 27 January 2020) recommended a primer pair targeting the V4 region of the 16S rRNA gene and ITS2 region for bacterial and fungal barcoding, respectively. Bioinformatics pipelines used for barcoding approaches are already well standardised and shared worldwide among the scientists, which makes possible the cross-comparison of various datasets from different labs. Unfortunately, this is not yet the case for the pipelines to analyse metagenomics datasets that are still under constant evolution, making cross-comparisons difficult.

Although microbial diversity, per se, is not strongly correlated with a particular functional capacity, it is clear that the loss of diversity can have an impact on microbial function (Thiele-Bruhn et al., 2012), at least for relatively specific functions performed by narrow microbial guilds or taxa. This applies even more when certain taxa are closely linked to very specific functions, including nitrifiers, methanogens, and arbuscular- and ecto-mycorrhizal fungi and biocontrol microorganisms like Trichoderma (e.g. Hartmann et al., 2009; Hayat et al., 2010; Lugtenberg and Kamilova, 2009; Peng et al., 2008; Singh et al., 2007; Xia et al., 2011). Therefore, the interpretation of the outcomes from microbial community-based testing tends to be straightforward and closely linked to Function 4 and Function 5.

Food web support (Function 2) of higher trophic levels no doubt starts from soil microorganisms and propagates through the trophic levels (e.g. earthworms) that are consumed by birds and mammals (Haynes, 2014; Scheu et al., 2002, 2005). However, the role of the microbiota in the soil food web is not fully understood, since many eukaryotic organisms can be considered meta-organisms, which carry their “own microbiome” that itself is essential for life-supporting functions. From this, it is unclear whether environmental microbiomes and host-specific microbiomes complement one another. So far there have been no comprehensive methods (especially not those addressing microbial functions) or standards available to address this problem. The use of stable isotope labelling of select carbon or nutrient sources as a promising approach to follow food webs and degradation pathways might provide one possibility in the future to assess food webs in soil. This would be accomplished by combining carbon and nitrogen stable isotope flux determination with phylogenetic analysis of the microorganisms labelled with the stable isotopes (e.g. Coban et al., 2015; Traugott et al., 2013; Lueders et al., 2004).

Methods to assess the biodegradation of pollutants (Function 3), as described above, are already implemented into ISO guidelines (Table 2) and are part of legal frameworks including pesticide directives (EU Regulation1107/2009/EC; European Commission, 2009). A number of standard methods for the determination of the potential of soils to degrade organic chemicals (Function 3) under both aerobic (ISO 14239, 2017) and anaerobic (ISO 15473, 2002) conditions are available. However, in the past, the development of standard methods was mainly driven by the need to assess the ecotoxicological effects of anthropogenic activities, such as chemical contamination of soils, rather than to describe and understand the natural properties and functions of soils. Defining methods for the determination of adverse effects of contaminants on soil biota was not only done by ISO, but was also a major task of other organisations such as the Organization for Economic Co-Operation and Development (OECD). For example, there are OECD guidelines, test nos. 216 and 217, for testing the long-term effects of single-exposure chemicals on soil microbial nitrogen and carbon transformation, respectively (OECD, 2000a, b). As a result, it was decided early that the standardisation of methods for toxicity testing should not be the primary aim of the ISO sub-committee (ISO TC 190/SC 4). Metagenomics lead to the rapid discovery of new genes, which catalyse degradation processes of xenobiotics and, consequently, offer new insight into the study of ecology of microbial degraders. The transfer of this knowledge into operational bioindicators for the estimation of soil filtration capabilities (e.g. by using qPCR or RT-qPCR assays to quantify those genes and their expression in soils, respectively) will be one of the major tasks in soil science in the upcoming years. Jeffries et al. (2018) for example were able to successfully predict the degradation rates of organophosphorus-based pesticides in a contaminated soil by using metagenomics-based functional profiling.

Some of the existing standard methods that are listed in Table 2 focus on the estimation of enzyme activities useful for soil quality assessment, which mainly contribute to Function 4. Here, the potential dehydrogenase activity measurement is an indicator of general (potential) oxidoreductase activity in soil. Since this measurement has been frequently used, there are large amounts of baseline data available on the toxic effects of a range of pollutants in soil. Recently, additional potential enzyme activities related to the C, N, P, and S cycle have been used and are either standardised or are in the process of standardisation.

The current evolution of molecular methods in microbial ecology has resulted in a large number of new endpoints. It is well known that many of the new endpoints (e.g. using quantitative real-time PCR (qPCR)) are more sensitive than classical methods that had been standardised in the past (Ribbons et al., 2016; Schulz et al., 2016). This new metagenomics approach will be of high importance in the future, as it allows for the implementation of information on new functional traits that can be standardised into an analytical pipeline. Direct sequencing of soil DNA extracts, called metagenomics, is nowadays a method that can easily be implemented to obtain an overview of in-soil living organisms, including microorganisms. It is recognised that metagenomics is no longer limited by sequencing possibilities, but more by the availabilities of large-scale computing clusters to analyse the amount of data generated. The future success of metagenomics in soil surveys will mainly depend on the possibilities to standardise bioinformatics pipelines as well as on the availability of tools for big data analysis and artificial intelligence. However, it must be mentioned that even a well-standardised and automated workflow will generate only data on the relative abundance of nucleotide sequences and not absolute values (Geisen et al., 2019). Thus at the moment for the assessment of new methods linked to Functions 4 to 8, qPCR from soil DNA extracts (ISO 17601, 2016) plays a very important role in determining the abundance of single-marker gene sequences, which are indicative of specific transformation processes or soil functions. For example, the quantification of nitrogen-fixing microbes, nitrifiers, and denitrifiers has been successfully implemented using the nifH, amoA, and nirS/nirK genes as markers, respectively (Henry et al., 2004; Hirsch et al., 2010; Ollivier et al., 2010; Sessitsch et al., 2006). Similarly, the quantification of microorganisms involved in the β-ketoadipate pathway has been implemented by targeting pcaH (El Azhari et al., 2008) and catA (El Azhari et al., 2010) gene sequences. Various methods for the assessment of soil microbial Function 4 (nutrient cycling), Function 5 (pest control and plant growth promotion), and Function 7 (greenhouse gas emissions) are proposed based on the qPCR analysis of gene sequence coding for enzymes which trigger the respective function (e.g. Fish et al., 2013; Ribbons et al., 2016; Smith and Osborn, 2009). Additionally, it should be noted that molecular methods based on the assessment of specific marker genes for estimating the degradation potential in soil have already been proposed for both PAHs (e.g. Cebron et al., 2008) and individual pesticides (e.g. Martin-Laurent et al., 2004). These could be interesting for future standardisation; however, if a method is very compound-specific and targeted, this could limit its application range. Thus, these specific approaches will not be discussed further in this article.

Major advantages of qPCR assays to quantify gene sequence numbers, which can be used as proxies for a given microbial process, are that they are (i) highly standardised, sensitive, selective, and reproducible, (ii) designed for high throughput analysis, (iii) available for a wide range of targets, and (iv) methods that are relatively cheap once the necessary analytical devices are on hand. Some training on the method is required; however, once trained the assays are easy to perform. For example, numerous studies have already used the microbial functional genes involved in nitrogen cycling to determine the status and to assess induced changes in the soil microbial community (Levy-Booth et al., 2014; Nannipieri and Eldor, 2009; Wallenstein et al., 2006). Consequently, the number of functional genes that are suited for use as specific indicators of soil function are continuing to grow in the literature as researchers gain experience in this field and data become more prevalent. Also, evidence is increasing that functional gene abundance and community structure are closely linked to related microbial activities and their increase or decrease, e.g. through agricultural fertiliser regime or soil contamination (Levy-Booth et al., 2014; Ouyang et al., 2018; Xue et al., 2018). However, contrasting findings have also been reported, pointing to the fact that functional gene abundance and diversity is less affected by short-term changes, e.g. due to soil moisture changes (Zhang et al., 2019). A critical meta-analysis of existing data and reports, respectively, would be timely to better identify and generalise the linkage of functional gene abundance and ecosystem services.

Disadvantages, on the other hand, are that (i) the quality of qPCR data depends on soil DNA extracts (PCR inhibition), (ii) primer pairs, even degenerated ones, might not successfully amplify all microbes of the functional group of interest, (iii) only genetic potential is resolved, and (iv) there is no differentiation between active, dormant, or dead microorganisms, when working with DNA as a template for the qPCR reaction. The analysis of total RNA and of mRNA, which could help to overcome the latter problem, is currently not a suitable alternative as it is highly dynamic in time and space and needs special care to stabilise the RNA extracted from complex environmental matrices to avoid its degradation. Another problem of DNA analysis is that the biological representativeness of the results is solely based on a relatively small amount of soil (from a few hundred mg to tens of g of soil) from which the DNA is extracted. The use of small soil samples (<1 g) simplifies the sample preparation process for molecular biologists; however, it provides a poor representation of the indigenous soil microbial community in the naturally inhomogeneous soil. Typically, the α-biodiversity declines with sample size, while that of β-biodiversity increases (Nicol et al., 2003; Penton et al., 2016). Lastly, it must be noted that the high repeatability and reproducibility of molecular biology methods, including qPCR assays, depends on extraction, purification, and amplification of DNA or RNA. This is typically performed using commercial extraction kits; however, simply changing the commercial supplier of a kit can substantially change the results (Brooks et al., 2015; Feinstein et al., 2009). This clearly challenges standardisation since standard methods must not hinge on a specific supplier.

Recently, molecular tools for the assessment of the microbial phosphorous turnover (Function 4) have been published (Bergkemper et al., 2016) where metagenomics data have been used for the construction of primers for P mineralisation, transport, and uptake. As another example, the relevance of anaerobic ammonium oxidation (anammox) for N cycling in soils has increased (Levy-Booth et al., 2014) along with the development of analytical methods for high throughput analysis. Among the microorganisms in soil that substantially govern pest control and plant growth promotion (Function 5), arbuscular mycorrhizae and ectomycorrhizal fungi are of high relevance. These microorganisms are especially abundant in the rhizosphere (Hartmann et al., 2009; Hayat et al., 2010; Lugtenberg and Kamilova, 2009). Methods related to Function 5 are listed in Table 3.

Several options exist for (additional) standardised methods to test Function 6 (carbon cycling and sequestration) (Table 3). For Function 6, there is a need to implement more fungal activity analysis as most tests described mostly assess bacterial activities. Thus, the integration of more fungal enzyme activities into the suite of standardised methods for soil quality assessment is essential (for example, determining the turnover of complex natural compounds such as lignin) (Baldrian, 2006). The ligninolytic enzymes laccase and Mn-peroxidase, as well as the chitin-degrading 1,4-α-N-acetylglucosaminidase, are typical fungal enzymes of interest for ecosystem services (Jiang et al., 2014; Šnajdr et al., 2008). However, since other organisms also produce these enzymes, including bacteria and plants (Bollag, 1992; de Gonzalo et al., 2016), current methods do not specifically target fungal enzyme activities. As a result, the implementations of molecular methods for assessing fungal communities are far less developed than those for bacterial communities (Table 3). The first approaches to close this gap have been made in recent years. For example, molecular systems to detect gene coding for laccases and other ligninolytic enzymes as well as other fungal activities in carbon cycling have been published and applied (Edwards et al., 2011; Chen et al., 2013; Hannula and van Veen, 2016). Also for genes involved in the fungal nitrogen turnover, primer pairs have been successfully developed (Gorfer et al., 2011). However, here, even more than for bacteria, it is critical to link copy numbers of genes directly to the size of the respective functional population, as in many cases one organism can harbour multiple operon coding for the same genes involved in a given function.

The method of community-level physiological profiling (CLPP) using the Biolog™ system (Biolog, Hayward, CA, USA) was first developed in the late 1980s to identify bacteria of clinical importance by assessing the consumption of 95 different carbon sources in a microtiter plate. The technique was then extended to identify bacterial strains from environmental mixed microbial communities samples using select carbon sources (Garland, 1997). Currently, the technique is frequently used to assess the effects of contaminants on soil microbial activity (Bloem and Breure, 2003; Schmitt et al., 2004). As such, the CLPP method has become a measure of microbial functional diversity in soil (e.g. Gomez et al., 2006) and was used to distinguish the biodiversity of soil microbial communities in monitoring programs (Rutgers et al., 2016). Even though the method is easy to use, it does have some drawbacks (Winding and Hendriksen, 2007). The technique is based on the utilisation of select carbon sources, which when consumed result in reduction, and thus colour change, of a tetrazolium indicator dye (Garland and Mills, 1991). This reaction is based on the dehydrogenase enzyme activity of cultivable, fast-growing, aerobic, eutrophic microorganisms (largely bacteria). Consequently, this technique does not reflect the full spectrum of microbial species within a mixed soil community. Additionally, due to the artificial growth conditions required in the test, it is argued that the method does not reflect the microbial community diversity and its function of a given soil (Glimm et al., 1997). On the other hand, however, standardised conditions allow for direct comparisons between microbial communities in different sites, for example, independent of the abiotic conditions, thus making CLPP a popular method for toxicology testing (Preston-Mafham et al., 2002).

Isothermal micro-calorimetry is another technique that involves the direct measurement of energetics in soil and provides a functional link between energy flow and the composition of belowground microbial communities at a high taxonomic level (Herrmann et al., 2014). With this method, an integrative determination of the metabolic activity of soil bacteria and fungi is achieved. The integrated assessment of substances' and energy turnover has high potential to elucidate the regulation of soil ecological functions. However, the substantial costs for the acquisition of this very specific instrumentation are considered a major drawback. Furthermore, the measurement requires water saturation of the soil and, thus, the samples are modified. Since calorimetry has been rarely used and data and publications are few, this method is considered not ready for standardisation.

The methods targeting thymidine or leucine incorporation into microbial biomass can be used to determine microbial growth rates and efficiencies (Bååth et al., 2001; Rousk, 2016). Growth rate is a fundamental reference for numerous other microbial properties and functions. For example, it is required to calculate microbial carbon use efficiency (CUE) as a key parameter describing C-substrate turnover and storage in soil (Liu et al., 2018; Spohn et al., 2016; Takriti et al., 2018). Furthermore, the method can be used to assess the adverse effects of toxic chemicals on the microbial community (Modrzyński et al., 2016; Rousk et al., 2009a). The drawbacks of these two methods are that (i) specific training is required, (ii) laboratories must have a permit to manipulate radioactive isotopes, and (iii) there are higher costs for proper handling and disposal of 3H-labelled radioactive material. As an alternative, the incorporation of the stable isotope 18O from labelled water into soil microbial DNA can be used to distinguish growing and non-growing microorganisms based on the gradient separation of [18O]DNA and [16O]DNA (Schwartz, 2007). The 18O stable isotope method has been improved by sequencing a marker gene from fractions retrieved from ultracentrifugation to produce taxon density curves, thus enabling researchers to estimate the percent isotope composition of each microbial taxon's genome (Schwartz et al., 2016). This method continues to be advanced and, although not used often, could have a high potential for future standardisation.

There are simplistic methods available to determine organic matter decomposition, which are indicative of C cycling (Function 6). The tests listed in Table 3 are based on measuring the weight loss of introduced organic materials of different complexity in soil over time. The tests are relatively easy to perform and inexpensive; however, degradation activity is not exclusive to microorganisms, but can also include invertebrates. The OECD litter bag test (OECD, 2006) for site-specific assessment of organic matter decomposition uses wheat straw as the substrate and provides clear evidence of cellulose degradation. In general, the litter bag tests provide evidence of the degradation of naturally occurring plant material in soil. Results do, however, depend on the mesh size of the litter bags (increasing exclusion of soil animals with decreasing mesh size). On the other hand, plant material or litter is hard to standardise, with the results largely depending on the composition of the plant material. As such, artificial cellulose has been successfully used for a laboratory procedure to assess organic matter decomposition (Kvas et al., 2017). Another alternative to the litter bag test is the use of tea bags (Keuskamp et al., 2013). Tea bags can be purchased to contain a consistent quality of material, and so this method is preferred by citizen science (e.g. farmers to assess the soil quality of their land). In order to better distinguish the degrading abilities of different soil microbiomes, the test could be modified to use different types of tea that contain recalcitrant material to a different extent. Another test for future method development is the bait-lamina test (ISO 18311, 2016) used to assess the degradation of organic matter in field soil by grazing invertebrates (Jänsch et al., 2013; Kvas et al., 2017). It is a simple test that can easily be adapted for use under controlled laboratory conditions (Jänsch et al., 2017).

Methods for the determination and assessment of greenhouse gas emissions from soil (Function 7) have already been standardised or are well advanced in the standardisation process (Table 2). They are mostly focused on measuring concentrations of greenhouse gases, like CO2, CH4, and N2O, as well as their fluxes as endpoints. In addition, molecular biology methods that estimate the relative abundance of functional microbial guilds or taxa give new insight into the ecology of microorganisms involved in the formation of greenhouse gases. For example, the qPCR measurement of key N2O functional genes has allowed researchers to link N2O reduction capacity to reduced greenhouse gas emissions in soil amended with organic matter (Xu et al., 2018). Additionally, the quantification of functional gene sequences related to methane generation and methane oxidation, respectively, yields detailed insights into the functional potential of climate change-affected permafrost soils (Yergeau et al., 2010).

For Function 8 (soil structure affecting soil water, gas balance, and filtration function), there is clear evidence that microbial activity and biomolecules substantially contribute to the formation and stability of micro-aggregates and thus to the structure, pore system, and pre-consolidation stress of soils (Six et al., 2004). While existing parameters, such as enzyme activities, are not clearly indicative in this regard (Beck and Beck, 2000), glomalin can be considered a biochemical marker of soil aggregation. This glycoprotein is produced by microorganisms, especially arbuscular mycorrhiza fungi, and significantly increases aggregate formation and stability (Rillig, 2004; Rillig and Mummey, 2006). The existing protocols for extraction (chemical extraction combined with autoclaving) and determination of glomalin, either by using the Bradford protein assay, enzyme-linked immunosorbent assay (ELISA), or the LC-MS method (Bolliger et al., 2008; Janos et al., 2008), open the possibility for its standardisation in the near future. It should be noted, however, that a well-equipped and experienced laboratory is required to perform this method.

As recently underlined by the European Food Safety Agency (EFSA) in a scientific opinion “addressing the state of the science on risk assessment of plant protection products for in-soil organisms”, there is an urgent need to modernise pesticide risk assessment by implementing specific protection goals for in-soil organisms which are key drivers of a wide range of functions supporting ecosystem services (Ockleford et al., 2017). There currently exists a multitude of methods that can potentially be used for this task. Here, we have identified in the body of this paper a number of methods that are presumably suitable for further evaluation and standardisation with regard to their scientific value and practical applicability. These prospective standardised methods will not only be useful to identify adverse effects on the soil microbiome, but also to conduct comparable studies in laboratories all over the world to define normal operating ranges of microbial activity in soil and respective quality indices and threshold values.

It is clear that all parameters taken together reflect the potential of a microbial community to perform a certain function and not solely a specific (actual) activity. This is important to understand in order to interpret the values of a given endpoint in relation to both energy fluxes and compound transformation rates, which can largely depend on intrinsic properties such as pedoclimatic conditions, nutrient availability as well as extrinsic properties such as anthropogenic effects, and soil cultivation measures. To make use of these methods as indicators of soil quality, there are several requirements that need to be included. These involve the assessment of the normal operating ranges of soil that include natural and dynamic fluctuations of a given endpoint. The methods need to be implemented into a framework, which takes into account site-specific conditions including soil type, pedoclimate, and land use. Undoubtedly, this requires further joint efforts in order to generate comprehensive databases from which normal operating ranges of values for a given proxy can be read. Such a task calls for standardised methods to obtain comparable data. Additionally, there is a requirement for the assessment of resistance and resilience of a given microbial endpoint to see how much it is affected by a soil disturbance and whether or not it can recover (e.g. return to its original state) after the disturbance has disappeared. Here the use of DNA-based methods, which provide a measure of a microbial community's potential to perform a given process, might be more useful than using RNA. The RNA rather indicates actual activities, which may highly fluctuate in time and space and thus are of less significance as an indicator. However, free DNA released from dead microbes is often highly resistant in soil, which might result in an overestimation of a potential function. This needs to be taken into account when interpreting the data. Recently, methods that extract DNA only from living cells have been described, but their use has not been introduced yet into recent standardisation activities.

Also, the use of a test battery to measure a range of interconnected endpoints is recommended (Ockleford et al., 2017) to integrate different biological and other parameters (e.g. soil pH, organic carbon content) into multiparametric indices (Bastida et al., 2008; Kvas et al., 2017). At present, it appears to be favourable to use a suite of different methods, i.e. functional gene analysis and microbial enzyme and/or degradation activities, for soil quality testing. Finally, to fully understand soil microbial functioning, a task was envisioned to investigate the linkage between the genetic functional potential and the available resources, termed the soil metaphenome (Jansson and Hofmockel, 2018). This will require even further integration and assessment of multiple parameters and test methods. Reaching that goal will surely promote soil ecological research but, at the current stage, may clearly go beyond the applied aim of standardisation to release easy-to-use targeted methods.

The critical evaluation of existing and non-standardised methods is required to further select and standardise new methods to assess soil quality. For methods linked to the molecular analysis of soil microbiomes, there is a need to ensure that worldwide activities are synchronised to propose important standards that are well accepted by the scientific community. To improve the reproducibility of data it has been agreed that a complex mixture of microorganisms (MOCK) must be implemented as a control in every experiment, but so far no common agreement on the composition of a MOCK community has been reached. However, it is clear that if further developments of microbial bar coding and/or metagenomics methods are to be implemented into ISO guidelines, a MOCK is required.

ISO standardisation committees are open circles and the presented selection and valuation of methods may not be complete. Environmental scientists are solicited to propose new work items enlarging the current catalogue of biological methods for future standardisation. Accordingly, this opinion paper aims at initiating a broader discussion intended to improve the measurement of microbial functions for soil quality assessment. Lastly, it must be noted that standardisation of methods is inevitably a balancing act. On the one hand, standardisation provides defined methods that are essential for obtaining comparable data, e.g. for integration into large, joint databases. On the other hand, it requires setting a specific method for several years. Consequently, scientific progress cannot be easily adopted, or at least with a delay, considering that standards are revised every 5 years, which may be a barrier to the introduction of new approaches resulting from technological evolution, especially in the fast-developing field of molecular biology methods. Hence, it is also the aim of this paper to have an open discussion to identify the best suitable methods with an assumed longer period of validity.