Concern-driven integrated approaches to nanomaterial testing and assessment – report of the NanoSafety Cluster Working Group 10

Background

Recognising nanotechnology as an enabling technology contributing to innovation, economic growth, employment and competitiveness, the European Union’s (EU) Commission, in its second regulatory review on nanomaterials, has reinforced its continuous commitment to promoting research and development in this area (Anon 2012a). Warranting the safety of nanotechnological products is seen as a crucial element in ensuring that the benefits of the new technology can be fully exploited. Therefore, up until the end of 2012, the Commission has funded a total of 46 nanosafety projects representing a total EU investment of 130 million EUR (Anon 2012b). To facilitate the formation of consensus on nanotoxicology, the Commission has requested EU-funded nanosafety projects to join forces through the so-called NanoSafety Cluster (Anon 2012b). The members of this initiative have assigned themselves the goal to identify key areas of nanosafety research which are likely to be of special significance in the coming years (NanoSafety Cluster 2011). Covering all aspects of nanomaterial characterisation, exposure and hazard assessment, research challenges relating to these key areas are further specified in topic-specific Working Groups. In delineating a timeframe for meeting such challenges, the NanoSafety Cluster has taken on the deadline of 2020, a year that has been spelled out by the Commission both in the Europe 2020 strategy for smart, sustainable and inclusive growth (Anon 2010a) and for the upcoming Research Framework Programme Horizon 2020 (Anon 2011a).

The present commentary summarises the outcome of the discussions of NanoSafety Cluster Working Group (WG) 10 on integrated approaches to testing and assessment (IATA) of nanomaterials (NM). Such approaches, in the literature also referred to as integrated testing strategies, are required for an adequate assessment of the impact of NM on human health and the environment. Whereas WG 10 has pursued its deliberations on IATA independently of existing regulations, they do stand in line with current EU guidance on NM safety testing. In the context of REACH Regulation 1907/2006 (Registration, Evaluation, Authorisation of Chemicals; Anon 2006), a testing strategy for NM should consider the procedure established for conventional chemicals expanded to address the specific peculiarities of NM (RIP-oN 2 2011).

One prominent trait of NM is the fact that, during the lifetime of a given NM, humans and the environment can be exposed to different forms of the material, for example due to agglomeration or aggregation, corona formation or interaction with surrounding organic material, or dissolution. Hence, it is of paramount importance for adequate testing to ensure that the testing conditions applied (including NM characteristics and exposure conditions) are appropriate to assess the risk under relevant real-life exposure situations. One aspect is that the physico-chemical properties of the nanomaterial during testing are known, either by analytical techniques or standardised techniques when suspending or dispersing NM for toxicity testing. One way or another, this issue needs to be addressed in the risk assessment strategy for NM.

Since a multitude of different NM in different exposure scenarios is expected, it will not be possible to perform all-embracing testing of all NM in all relevant scenarios. Instead, testing must be targeted to the actual concerns for a given NM making use of realistic exposure scenarios. Moreover, a testing strategy should include possibilities for the grouping of NM (e.g., by applying a “read-across” methodology, some tests could be waived based on a categorisation of NM), and should also aid the grouping concept itself (e.g., the testing strategy should provide information that is relevant for grouping).

The actual concerns associated with a given NM should be determined in relation to material properties, specific exposure situations, biokinetic data and/or markers of early biological effects. They should be used to define the crucial human health and environmental end points to be tested in focused studies, including the test designs of these studies. All of these issues should be considered for the grouping of NM which, in return, should form integral part of the IATA. The integrated NM toxicity and ecotoxicity testing approaches proposed in this commentary are based on these considerations.

State-of-the-art

Multiple toxicity studies with NM have been carried out in the last decade. However, most of them used non-standardised testing protocols leading to sometimes not reproducible and hardly comparable results, which therefore are insufficient for univocal hazard and risk assessment. In addition, the unavailability of consistent physico-chemical characterisation data in the same studies makes it difficult to identify which (combinations of) material characteristics determine the documented toxic effects. One reason behind the lack of convincing patterns could be that characterisation has been performed ex situ, since NM are generally difficult to characterise in situ (Tiede et al. 2008, Card & Magnuson 2010). Nevertheless, it has been shown that a variety of factors such as ionic strength, pH and other media-specific properties cause changes to the primary NM once they enter media (e.g., related to NM agglomeration, aggregation and surface modification), which affects both their bioavailability and toxicity (Hassellov et al. 2008). Besides, the results are derived using a variety of dispersion and analytical protocols and here again standard methods require to be developed.

Current toxicological approaches to assess hazards of NM are either based on methods adopted from classical toxicology or on alternative methods. These approaches do not fully consider the unique aspects of NM, for example, 1) different forms of a given NM in different biological media; 2) uptake/absorption, distribution, corona formation and elimination/deposition (ADCE, used by analogy to ADME, absorption, distribution, metabolism, excretion; since, for most NM, metabolism, unlike corona formation, does not play a major role); 3) functional impacts at the organ and cellular levels.

Slow elimination and persistence are main drivers for bioaccumulation. Similar to conventional hydrophobic persistent chemicals, such as DDT, that are resistant to environmental and biological degradation, NM have the potential to accumulate in humans and biota (food chain) when exposure takes place on, for example, a daily basis. Presently, the structure and dynamics of protein corona are considered to be key to the nanoparticle’s rate of uptake and transport into cells and final subcellular localisation (Nel et al. 2009; Lundqvist et al. 2011). A number of proteomics methods to identify the nature, composition and dynamics of the biomolecules associated with NM have been developed (Lai et al. 2012). Without suitable information on the potential for NM to bioaccumulate, it is not possible to carry out higher-tier human health or environmental risk assessment or to derive environmental quality standards (Anon 2008).

While the risk assessment of conventional substances is based on the notion that their chemical identity governs the biological effects of a substance, there is general agreement that the toxicity of NM is determined by a set of characteristics, for example, size, shape, surface area, charge. Given the substantial diversity within each group of nanomaterials and the complexity of nanosystems (e.g., stability of dispersions under different conditions), a large number of property combinations need to be considered in order to assess the overall hazard of a single material type. Currently, it is widely accepted among scientists and regulators that the hazard/risk assessment of NM can only be addressed on a case-by-case basis. However, considering the large number of existing and emerging nanoformulations, this would be a time and resource intensive task, conflicting with the 3Rs principle to replace, reduce and refine animal testing (Russell & Burch 1959) implemented in EU Directive 2010/63/EU on the protection of animals used for scientific purposes (Anon 2010b). In this context, IATA have become particularly relevant since they are intended to speed up the risk assessment process, while at the same time reducing testing costs and animal use by effectively exploiting all existing data (van Leeuwen et al. 2007; Hartung 2009). Integrated processes consolidate all available information (including both exposure and toxicity information) to identify relevant concerns and to determine the information that best addresses these concerns (focusing on toxicity studies and/or exposure information).

The need for standardisation and new approaches in the nanosafety area has been recognised. In parallel to ongoing scientific research, a number of international initiatives have been launched, such as the OECD Working Party on Manufactured Nanomaterials (OECD WPMN; see: http://www.oecd.org/env/ehs/nanosafety/ note: all websites were accessed in February and March 2013) and the ISO Technical Committee 229 (see: http://www.iso.org/iso/iso_technical_ committee?commid=381983).

Of particular importance for the above discussions are the OECD WPMN Steering Groups (SG) 6 and 7. SG 6 deals with risk assessment approaches, such as “read-across” methodologies, and SG 7 addresses the use of alternative test methods and integrated testing strategies for NM hazard assessment. This SG has proposed a new short-term inhalation study (STIS) for NM testing (OECD 2011) and has compiled a list of in vitro methods that might be used for NM human hazard identification. Furthermore, it has initiated a similar discussion for environmental impacts. Comparable structures of the human and environmental hazard identification frameworks aim at allowing a better integration of human health and ecological risk assessment into one coherent strategy and at facilitating its implementation for regulatory purposes.

Vision beyond the state-of-the-art

The NanoSafety Cluster vision 2020 foresees the development of a concern-driven guidance for investigating potential risks of NM. This will enable focused research on NM that may be of particular concern based on (expected) exposure levels and exposure routes, material properties as well as in silico, hazard and biokinetic data. By advocating that animals are only used for crucial and focused studies minimising numbers of animals used and the distress inflicted upon the animals, this approach further meets the provisions of EU Directive 2010/63/EU (Anon 2010b).

Based on these considerations, IATA will be developed allowing for different sequences of testing depending on the types of NM. Such IATA will start out by identifying relevant concerns, based on NM exposure and use scenarios and taking into account already available toxicological information and basic information assessed by non-testing (structure–activity relationships (SAR), generic physiologically based pharmacokinetic (PBPK) modelling based on in vitro data, and grouping), proceeding with tests using acellular systems and then cellular systems, up until in vivo, long-term testing approaches, if deemed necessary (Johnston et al. 2013). These strategies will be based on a thorough understanding of the biokinetics of a given NM in exposure-relevant media and matrixes (e.g., medium-dependent agglomeration, dispersion, etc.) enabled by a continuous sampling, analysis and characterisation paradigm. They will be designed both for human health and environmental safety/risk assessment, for example, by mimicking realistic exposure scenarios and by using appropriate dose levels for different purposes and in different situations. Finally, these strategies will be based on validated methods with established predictive power.

Such guidance, to be fully developed and effective by 2020 and beyond, will require less testing whenever the available information is sufficient and adequate for decision-making. For instance, if an NM rapidly dissolves, the substance should be treated as a conventional chemical, although the assessment of dissolution, and under which conditions and in which media, could be the actual, underlying challenge (remaining to be addressed in future research projects, such as NanoREG; see: http://ihcp.jrc.ec.europa.eu/our_activities/nanotechnology/symp2012/doc/van_Teunenbroek_Research_Reg_needs_s2.pdf). At the same time, it will be possible to obtain more information from the selected tests, for example, on the particles’ mechanism of action (Rossini & Hartung 2012; Nel et al. 2013). Nevertheless, the guidance might also imply requiring more information if it is necessary to address specific concerns (e.g., immunotoxicity, cardiovascular toxicity, neurotoxicity, developmental toxicity). Eventually, it will be inevitable to discuss which level of certainty on the potential risks of a given NM in a specific application should be required.

Furthermore, by 2020 and beyond, guidance will be developed and effective on when NM (based on physico-chemical characteristics, exposure and early biological effects) can be grouped, how these groupings should be constructed and what kind of information is necessary to be able to group. In addition to avoiding extensive hazard testing of NM, this will also provide insight into the conditions under which information on exposure and hazard for NM can be used for risk assessment purposes (Som et al. 2012).

This vision 2020 of the NanoSafety Cluster should be realised in the context of existing international and national chemical regulatory frameworks taking into account existing OECD Test Guidelines (TG) and adapted as appropriate to take into account the specific properties of NM, as recommended by the OECD Chemicals Committee (OECD 2013). Following on a mid-term evaluation of the OECD’s nanosafety programme in 2012, the Chemicals Committee, a parent body to the WPMN, additionally recommended updating existing OECD TG or including new ones in the light of experience with NM, to apply the OECD principles of Good Laboratory Practice to NM safety testing, and to make safety data related to NM available to the public (OECD 2013).

NM dispersion and in situ characterisation for toxicity testing

On the one hand, meaningful exposures allowing to understand and monitor the important characteristics of real-life exposure and to correctly interpret the test results cannot be mimicked in all toxicological test systems (Hristozov et al. 2013). On the other hand, the form of the NM (agglomeration state, corona, etc.) can be largely dependent on the exposure scenario. Therefore, test sample preparation by dispersion of the respective NM is a critical step for toxicity testing, and it must be well considered and appropriate (Rothen-Rutishauser et al. 2010). Likewise, the resulting test sample dispersions (both stock and test solutions) have to be characterised. Over the past years, multiple dispersion protocols have been used and an extensive list of parameters for in situ characterisation has been proposed (Schulze et al. 2008; Card & Magnuson 2009; SCENIHR 2009; OECD 2010). Figure 1 lists characterisation parameters currently considered relevant for NM preparation and safety testing.

Testing strategies to assess NM biopersistence and biokinetics

NM may potentially cross portals of entry into the body, such as the gills, the gastrointestinal tract, lung epithelium or skin, and also internal barriers, such as the blood–brain barrier, placenta and blood–testis barrier. NM with different characteristics (size, coating, shape) may differ considerably in the extent of their transportation across these barriers. The types of particles that can be transferred across barriers have not been systematically investigated, and to date very little is known about the parameters that influence differences in the extent of transportation (Oberdörster 2009; Landsiedel et al. 2012). However, such information will be relevant to determine if NM have reached the systemic circulation, and if so, to what extent bioavailability is increased, and whether, for instance, systemic effects, including cardiovascular or immunological toxicity, should be considered.

In contrast to many soluble chemicals, NM generally tend to disappear rapidly from the blood by being taken up into tissues, mainly those containing phagocytic cells. The apparent very short blood-plasma half-life stands in sharp contrast with the apparent long whole body or tissue half-life. Once filtered from the blood by macrophages, NM tend to stay in these cells and in similar cell types, and they undergo whole-body elimination only to a fairly limited extent. Strong indications for this are already available for a number of NM, such as silver, SiO₂ and cerium nanoparticles (Lankveld et al. 2010; Dan et al. 2012).

Coatings as intentional modifications of the NM surface impact the effect on organisms by for example, increasing the blood-plasma half-life (such as in the case of polyethylene glycol (PEG)-coated NM). Likewise, unintentional surface modifications may have an impact on the tissue distribution of NM, as well as on the rate in which distribution occurs (Liu et al. 2012). A “protein corona” is likely to be formed around the NM when they enter the body or even already before, for example, when they are added to food products (Nel et al. 2009; Lundqvist et al. 2011; Johnston et al. 2012). It should be noted that the corona of biological molecules covering the NM surface is most likely composed not only of proteins, but also of lipids and carbohydrates (Gasser et al. 2010). This “bio-corona” surrounding NM is dynamic, since the types of molecules forming it may change in time. Additionally, proteins and other molecules in the body fluids (mucus, blood, etc.) can differ significantly depending on the individual’s health conditions, thereby affecting the composition of the corona (Nel et al. 2009; Johnston et al. 2012). Similar to surface modifications of the NM, the corona affects the distribution pattern and the rate of distribution. This also implies that the uptake into cells is driven by the corona (Nel et al. 2009; Landsiedel et al. 2010). Concerning ecotoxicity, NM coating with organic molecules, such as humic acids or with minerals, is of relevance. More evidence is becoming available in regard to such issues, but this is still far too little to obtain a clear overview on the influence of NM surface modification and corona on bioavailability, biokinetics and cell entry.

Effects of NM may be related to 1) the particles themselves and their coatings (particle effects); 2) ions or molecules released from the particles (chemical effects) and 3) molecules formed by the catalytic surface of the particle (nanorelated effects) (Landsiedel et al. 2010; Nel et al. 2013). In vitro dissolution tests in physiologically relevant media (e.g., lysosomal fluid, gastrointestinal fluid, lung lining fluid) may give indications on the time frame in which mainly particles, both particles and ions, and mainly ions are present (Dekkers et al. 2011, 2012; EFSA 2011). If particles are unlikely to dissolve, efforts should focus on long-term particle-related effects, since the particles are likely to accumulate over time and exert their particle effects accordingly (Dekkers et al. 2012). If particles dissolve, both particle and ion-related toxicity should be considered. In that case, accumulation of particles is to be expected to a smaller extent, due to elimination by dissolution of particles to ions. The ion-related effects may be different from the effects of the dispersed particles. If NM distribution and cellular uptake occurs in the particulate form, the ions may be released at different sites than when the NM are distributed as dispersed particles. Hence, the resulting toxicity may be different.

Uptake by cells without significant clearance from those cells, as known for some NM, may pose a potential risk that up to now has not sufficiently been taken into account in the context of risk assessment. In order to prevent problems from arising, such as those encountered for persistent organic pollutants, information on long-term effects of NM should be addressed.

In conclusion, the biokinetics of NM is certainly a research area of high priority. By 2020, the understanding of the mechanisms and significance of NM absorption via different routes, including de-agglomeration, and their distribution and translocation throughout the body, as well as cell type-specific NM uptake, breakdown and excretion will have markedly improved. Furthermore, the significance of biological barriers will be better understood and can be estimated based on simple tools (in silico, in vitro), allowing for a high-throughput and reliable assessment of the possible risks posed by NM to human health and environmental species. Kinetic data and kinetic modelling should become tools to evaluate whether a specific NM behaves differently from another NM or from the corresponding bulk material. This should also allow assessment of whether NM can be grouped for risk assessment purposes. Based on such mechanistic understanding, it may also become possible to predict under which circumstances overload of various cell types is likely to occur.

Testing strategies to assess NM human health hazards (i.e., toxicity)

To date, no new type of toxic effect has been described for NM (i.e., no effects which have not been observed with any other substance or particle before). However, as has been discussed above, the uptake, tissue distribution and clearance of NM may be different from dissolved molecules or larger particles. Nevertheless, the toxicity of NM can generally be tested by standard testing methods used for conventional chemicals, adapted to take into account, for example, the NM-specific requirements for test sample preparation and characterisation as well as test interference controls. Further adaptations of standard test methods may be necessary. It should be noted that these adaptations might not only be relevant for NM testing, but that they might be challenges for the modernisation of safety testing approaches as such.

Traditional toxicity testing is largely restricted to the mere observation of apical effects (i.e., clinical or histopathological manifestation of effects) and was performed according to an extensive list rather than a targeted strategy. A targeted testing strategy would be an efficient approach in line with the 3Rs principle: fewer animals might be needed for testing, or more – and more relevant – information would become available with the reduced numbers of animals used (Silbergeld et al. 2011). A modern and efficient approach would address specific concerns for the respective NM in its given area of use (Nel et al. 2013).

A concern-driven NM toxicity testing scheme consisting of three main tiers is presented in Figure 2. Tier 1 includes a concern assessment based on the physico-chemical characteristics of the specific NM and relevant scenarios for potential exposure, depending on its envisaged use. Such relevant exposure scenarios should take into account realistic dose levels that for example, workers or consumers might be exposed to and whether nanomaterial exposure is likely to be in the aggregated or agglomerated states. For NM of concern identified in tier 1, tier 2 focuses on identifying their basic toxicological concerns, while tier 3 provides options to study specific end points of concern in more detail. The need for the performance of specific tests in the last tier is determined by the combined results of the first two tiers (Zuin et al. 2011; Cockburn et al. 2012).

Tiers 2 and 3 each consist of three parts, the so-called toxicity domain, the decision-making process and the description of options for testing within each domain. Each toxicity domain reflects a specific toxicity end point or type of testing (e.g., repeated dose, biokinetics) to be addressed and contains a number of options for testing or non-testing (e.g., grouping/waiving) that can be selected in the decision-making process based on the concerns identified in the preceding tier(s).

These three tiers of the concern-driven toxicity testing strategy for NM are discussed below.

Testing strategy to assess NM impact on the environment (i.e., ecotoxicity)

A variety of methods and approaches for assessing the ecotoxicity and bioaccumulation of NM is already available, and further ones are under development. Underlining the fundamental difference between human health hazard and environmental hazard assessment, Figure 4 illustrates the main building blocks (i.e., different types of test methods and purposes of testing) of ecotoxicity testing strategies. These consist of laboratory tests, on the one hand (Figure 4; building blocks 1a, 1b and 1c; in blue, with building block 1c in light blue, underlining that relevant test methods for this building block remain to be developed), and environmental simulation studies (Figure 2; building block 2; in green). Subsequently, Figure 5A and B present a proposal on how to integrate these building blocks into a tiered ecotoxicity testing strategy for NM.

For assessing the impact of NM on the environment, both ecotoxicity and bioaccumulation will be determined making use of standardised laboratory test systems (Figure 4, building block 1a), similar to the standardised procedures established for conventional chemicals (e.g., according to OECD TG). In these test systems, standardised, and often artificial, test media are employed. Therefore, they only allow a general characterisation of NM effects, and verification of the results from such tests taking into consideration environmentally relevant groups of organisms (building block 1b) and realistic environmental exposure scenarios may be necessary (building block 2) (von der Kammer et al. 2012). The complex interactions between NM, test media and organisms may require amendment of existing TG. Furthermore, the information obtained in standardised test systems is limited with regard to determining modes of action of the NM. This information (Figure 4, building block 1c) may, however, be required for classifying NM, and it is likely to be a prerequisite for reduced, efficient testing aimed at a practical assessment of NM environmental hazard. Such suitable test systems beyond standardised testing, however, remain to be defined (Klaine et al. 2008; Handy et al. 2012a, 2012b).

Likewise, further research is required to define which test systems are applicable for screening or confirmatory testing of the compliance of standardised laboratory tests using more specific tests with environmentally relevant organisms (Figure 4, building block 1b). Depending on the potential environmental concerns identified in basic laboratory testing, further test species, end points and food webs (interspecies transfer) might be studied in environmental simulation studies applying more realistic environmental exposure scenarios (Figure 4, building block 2).

Since NM bioavailability is highly dependent on the chosen test conditions, care has to be taken when simulating environmentally relevant exposure. In this context, sedimentation and (hetero-)agglomeration of the NM or application of natural stabilisers, such as humic acids, and their variability under different environmental conditions have to be taken into account (Handy et al. 2012a, 2012b). Apart from providing data for environmental risk assessment, the results of environmental simulation studies performed under environmentally relevant exposure conditions can be used as basic information for environmental monitoring. Compartments, habitats, feeding types or organisms identified as potentially endangered can trigger the need to collect specific environmental samples. Due to methodological limitations, however, such deliberations are currently speculative.

Due to the diversity of NM in regard to type of material, shape, size, surface modification, crystalline structure, etc., for efficient ecotoxicological testing it is of special importance to be able to define groups of NM. Specific groups may comprise NM with comparable fate, behaviour and effects in the environment, as determined with the applied testing strategy (Stone et al. 2010). To obtain comprehensive information on the properties and effects of a given group, a sufficient number of materials belonging to it should be studied in detail. For further NM belonging to the same group, only recognised key parameters, such as the most sensitive end point making use of environmentally relevant organisms, remain to be addressed (Figure 4, building block 1b).

Based on these building blocks describing different purposes of ecotoxicity test methods, a tiered testing strategy to assess environmental hazards is proposed in Figure 5A and B. Testing begins with a selection of those tests considered necessary for the given NM (Figure 5A; tier 1). (In this context, it remains a matter of further investigation to determine whether information from human toxicity tests is useful in supporting the selection of ecotoxicological end points). Depending on the main exposure path (i.e., water, sediment, soil), testing should be performed in aquatic, sediment and/or terrestrial species. Furthermore, it is advisable to include long-term testing alongside short-term testing from the beginning due to the persistent nature of many nanoparticle types.

In the context of REACH, the choice of test systems and test organisms to be used for ecotoxicological testing of conventional chemicals depends on the production volume of the respective substance. In the case of NM, however, it seems more appropriate to base the testing scheme on expected concerns based on routes of exposure, findings on physico-chemical properties and on fate studies, rather than production volume. Such an adaptation of the testing scheme seems permissible since the REACH guidance documents (ECHA 2012) allow adapting the testing strategy in specific cases. Exposure route-driven selections of test systems are considered to be most appropriate, if exposure in soil and sediment is more likely than in pelagic systems. This may not always be the case, although one might intuitively assume that NM tend to agglomerate/aggregate and sink. Furthermore, higher exposure does not always equate with higher risks.

All test results are compared with triggers (qualifiers). For conventional chemicals, such triggers are based on a comparison of the expected environmental concentration to the effect on mass basis corrected by assessment factors. It remains to be determined whether triggers comparable with those used for the testing of conventional chemicals can be applied for ecotoxicity testing of NM or whether modifications are required. For NM, expression of the environmental concentration on mass basis may be less suitable, and particle number concentration instead of mass concentration may be an appropriate alternative. To address these issues, further knowledge on NM exposure and fate are necessary. If such triggers are exceeded in tier 1 test results, tier 2 testing has to follow.

In tier 2 of the ecotoxicity testing strategy (Figure 5B), only the specific group of organisms or the environmental compartment has to be considered for which a potential unacceptable risk was identified in tier 1. In step 1 of tier 2, further tests with further species, laboratory-scale simulation systems and mode-of-action tests are performed as appropriate. In the second step of tier 2, nanospecific aspects of particle exposure have to be taken into account: Since the testing conditions can affect surface functionalisation, agglomeration behaviour and bioavailability, it might be advisable to consider using natural stabilisers, such as humic acids, or to apply NM by simulating environmentally relevant pathways of entry. Analytical verification of the physico-chemical characteristics of the NM during testing may be necessary. Since environmental conditions are highly variable, such simulations can only cover a limited number of different scenarios.

Due to prevailing knowledge gaps in the area of environmental hazard assessment of NM, further research is needed to confirm and complete the proposed ecotoxicity testing strategy. Such research should address the following topics (Aschberger et al. 2011):

• NM solubility, agglomeration and heteroagglomeration processes in environmentally relevant media.

• Selection of test organisms and end points for full NM testing (in standardised laboratory test systems): based on concern, related for example, to route of entry, rather than production volume?

• NM modes of action: elaboration of suitable methods.

• Criteria for classifying NM (particle characteristics vs. mode of action).

• Confirmatory tests: Which organisms and end points should be considered? Are the test methods that proved most sensitive for the NM respective category sufficient?

• Definition of triggers and qualifiers: Are the procedures applied for the testing of conventional chemicals suitable for NM?

Grouping of NM for human health and environmental hazard assessment

Numerous NM are likely to find widespread applications in the near future, and a much greater number of modifications and uses of these NM is expected. It will be impossible to perform a full testing program on all NM with all modifications and in all use scenarios, notwithstanding that modifications or use/release scenarios may alter their biological effects (Som et al. 2012). Alternatively, it seems possible to assign certain biological effects to specific material properties (physical properties and chemical and sterical composition) and group NM based on these material characteristics (Zuin et al. 2011). Even though many NM have been shown to interact with cellular systems in vitro (inducing inflammation, ion release, catalysis of the formation of reactive species or direct mechanical interaction), grouping of NM based on material characteristics has only been partly successful to date. So far, no single material property – be it surface, volume or generation of reactive oxygen species – perfectly correlates with the observed biological effects for various types of NM. Therefore, grouping of NM should be a high research priority for the next years.

As illustrated in Figure 6, alternative or complementary groupings of NM may be based on:

• Similar biopersistence and biokinetic characteristics. Fate and kinetics may also give a measure for grouping/summing nanomaterials, for example, if the distribution and mode of action are the same, but the bioavailability is different (due to differences in size). Identical distribution patterns in tissues or environmental compartments might also be a criterion for grouping different NM. If a nanomaterial shows a deviating distribution pattern, this may result in different effects and/or different target species for environmental exposure.

• Similar or common biological effects, including early effects and NM cell structure interactions. The latter approach can be served by cellular assays as well as short-term in vivo tests.

These specifications reveal that a given NM could belong to more than one group. Furthermore, grouping based on early biological effects is tightly linked to the adverse outcome pathways concept (Ankley et al. 2010; OECD 2012) and the so-called Tox21c Initiative in the USA (Firestone et al. 2010). Hence, grouping of NM by concern is considered a potential route.

Grouping of substances should form an integral part of any NM testing strategy. In the course of NM toxicity and ecotoxicity testing, it seems an effective and efficient approach to combine exposure, fate, biokinetics and hazard data for risk assessment and grouping purposes. This document envisions a guidance regarding the integration of material properties, exposure, biokinetics and hazard data, which therefore should be a high priority for future research on the safety assessment of nanomaterials.

Recommendations for the human health and environmental hazard assessment of NM