Journal of Nanoparticle Research

, Volume 12, Issue 2, pp 383–392

Redefining risk research priorities for nanomaterials

Open AccessPerspectives

DOI: 10.1007/s11051-009-9829-1

Cite this article as:
Grieger, K.D., Baun, A. & Owen, R. J Nanopart Res (2010) 12: 383. doi:10.1007/s11051-009-9829-1


Chemical-based risk assessment underpins the current approach to responsible development of nanomaterials (NM). It is now recognised, however, that this process may take decades, leaving decision makers with little support in the near term. Despite this, current and near future research efforts are largely directed at establishing (eco)toxicological and exposure data for NM, and comparatively little research has been undertaken on tools or approaches that may facilitate near-term decisions, some of which we briefly outline in this analysis. We propose a reprioritisation of NM risk research efforts to redress this imbalance, including the development of more adaptive risk governance frameworks, alternative/complementary tools to risk assessment, and health and environment surveillance.


NanomaterialsNanotechnologyResearch prioritiesRisk assessmentRisk governanceSocietal implications


While global sales of nanoproducts are expected to reach € 450 billion within the next year (Hanssen et al. 2008), scientists and regulators are still left with many questions as to whether nanomaterials (NM) pose a risk to human health or the environment. The risk assessment framework developed for chemicals remains the predominant decision support tool, underpinning regulations that cover NM or providing information to make the case for regulatory amendment (Rocks et al. 2008). This framework is well known to many, comprising hazard identification, hazard assessment and risk characterization (including considerations of exposure) (Rocks et al. 2008; EPA 2009; Owen et al. 2009b). Associated uncertainty in the process can be managed, for example by the application of safety factors (European Commission 2003; Owen et al. 2009b). While it is recognised that methodologies underpinning the conceptual risk assessment frameworks (e.g. EU Technical Guidance Document (TGD), Organisation for Economic Co-operation and Development (OECD) Test Guidelines) may not be entirely fit for purpose (e.g. Crane et al. 2008), the general consensus has been that in principle the chemical risk assessment framework is sound to use for NM with some modifications (European Commission 2008b; OECD 2008a; SCENIHR 2007, 2009).

Whereas, in principle, risk assessment is a sound approach, in practice, it is not an easy task to complete as there are some very significant challenges to first overcome (e.g. Maynard et al. 2006). It is now acknowledged that its completion will quite possibly take decades even for those NM that are currently on the market, let alone those that are emerging. Similar challenges have been faced for other chemicals (e.g. endocrine-disrupting chemicals, Sumpter and Johnson 2008). However, NM may represent an extreme case due to their diversity (e.g. particle sizes, functionalities) and range of applications (Owen and Handy 2007; RCEP 2008; Linkov et al. 2009a). While the question of identifying the most appropriate mechanism(s) to support timely decisions (e.g. interventions) in the face of little or no data is far from new (Collingridge 1980), it may be more challenging for NM and, at the same time, of utmost importance given the ubiquitous nature of nano-embedded consumer products and applications (Project on Emerging Nanotechnologies 2008). Some fundamental questions concerning whether NM risk research efforts have been directed in the most effective fields for timely decisions regarding environment, health and safety risks include: How do research efforts compare between the fields dedicated to using traditional risk assessment frameworks and alternative or complementary frameworks or tools for NM? Are programs that feed into chemical-based risk assessment made at the expense of research into tools that can support near-term decisions? What are the alternatives to traditional risk assessment currently available and what are their strengths and weaknesses? This analysis aims to address these critical questions, in addition to providing a snapshot of publications, projects and funding schemes made in these fields. We then propose some recommendations for future NM risk research schemes to help ensure the responsible innovation of NM as well as ultimately protect human and environmental health.

Risk assessment as a decision support tool: challenges posed by nanomaterials

Scientists, international organizations and regulatory agencies have been actively working towards developing risk assessment for NM in recent years (e.g. NNI 2008b; EPA 2009; OECD 2009d; SCENIHR 2007, 2009). In general, it has not yet been possible to complete individual NM risk assessments (SCENIHR 2009) due to extensive uncertainties and knowledge gaps within nearly all aspects of the risk assessment process (RCEP 2008; Grieger et al. 2009). Among other challenges, there is a distinct lack of quantitative exposure and hazard data for both humans and environmental species for many NM (Crane et al. 2008; Handy et al. 2008; SCENIHR 2009; Wiesner et al. 2009). In addition, a number of key methodological concerns have been raised, including uncertainty in applying standardized test methods developed for chemicals to NM (e.g. to quantify hazards including sample preparation for (eco)toxicity studies, characterisation of NM in test systems, dosimetry and reporting metrics) (Crane et al. 2008; Powell et al. 2008; Shatkin 2008). Furthermore, there are also difficulties in detecting and quantifying NM in complex environmental matrices (Owen and Handy 2007; Hassellov et al. 2008).

Based upon a reflection of these challenges and in response to calls for more research (e.g. Maynard et al. 2006), increased efforts regarding these have been underway. For example, scientists and organisations have been actively generating and analysing data for effects and exposure assessments as well as reviewing risk assessment methodologies for their appropriateness for NM. Academics and scientists in government and regulatory agencies all play a role in these developments, as well as industry, for example under chemicals legislation in relation to NM (e.g. Registration, Evaluation, Authorisation and Restriction of Chemical substances, REACH) (European Commission 2008b).

In the EU, the European Commission’s Scientific Committee on Emerging and Newly Identified Health Risks (SCENIHR) has recently reviewed the available data for risk assessment of NM (SCENIHR 2009). They conclude that the risk assessment framework seems applicable to NM although they acknowledge and describe many of its limitations, stating that the risk assessment process is still under development. Others such as the European Food Safety Authority have recently published similar conclusions, stating that although there are some major (e.g. methodological) challenges, current risk assessment methodologies are expected to be applicable for NM in food and feed applications in principle, and assessments should be undertaken on a case-by-case basis (European Food Safety Authority 2009).

The challenges for risk assessment posed by NM are reflected by a significant program of work at the Organisation for Economic Co-operation and Development’s working party on (manufactured) NM (WPMN). An array of projects are being directed, including the development of a NM risk research database (OECD 2009d), analysis of test methods (which underpin chemicals risk assessment) as applied to NM and a sponsorship program that will acquire risk assessment data for 14 NM of current relevance (OECD 2008b). Further study has also been undertaken to prioritize research needs to close the known knowledge gaps as quickly as possible, supporting the performance of risk assessments often in the context of current regulatory testing requirements (DEFRA 2006, 2007; Maynard et al. 2006; ICON 2008; NNI 2008b; Elder et al. 2009; SCENIHR 2009).

On the whole, a consensus is beginning to emerge: risk assessment frameworks for chemicals should be appropriate for NM, but they most likely need some methodological modifications. Exactly what modifications are needed is not consistently made clear, and how long it will take to make these modifications is also not often stated.

Despite these serious technical challenges that risk assessors face, most knowledge gaps are expected to be reduced in due course because of their epistemic nature (RCEP 2008; Grieger et al. 2009). It is anticipated that eventually standardized testing methodologies and analytical tools will be developed alongside full NM characterization and dose–response data (ISO 2008a, b; OECD 2008a, b). History has shown many examples in which regulatory test methods were developed and applied (Baun and Hansen 2008; OECD 2009a, b) in response to new knowledge (e.g. endocrine-disrupting chemicals, Sumpter and Johnson 2008), and later test methods were developed (OECD 2009a, b). In fact, a recent review of the applicability of OECD test guidelines for NM (OECD 2009e) shows this process in action: some test guidelines for NM physical chemical properties appear to be adequate for NM (e.g. TG 102, 109, 113, 116), some may be applicable in some cases or for some NM (e.g. TG 101, 105, 106, etc.), while other guidelines are considered inadequate (e.g. TG 103, 114).

However, how long will this process take especially given the diversity of NM and applications? A recent analysis estimates that testing existing nanoparticles in the USA alone will cost between $249 million and $1.18 billion and take 34–53 years for completion (Choi et al. 2009). Earlier analyses also estimated, at least, a decade for the acquisition of some critical knowledge within the field (Maynard et al. 2006). Given this, some have suggested that more rapidly deployable decision-support frameworks and/or tools need to be applied now (Hansen 2009; Linkov et al. 2007, 2009a; Mantovani et al. 2009; Metcalfe et al. 2009). In addition, others have proposed the need for risk governance1 mechanisms that can be enacted far earlier in the nano-innovation process, reducing the time needed to acquire critical risk characterisation data (Lee and Jose 2008; Owen et al. 2009a). In some cases, the precautionary principle2 has been invoked to support decisions in the absence of full scientific certainty. For instance, the Environment Agency in the UK recommended that unbound carbon nanotubes are treated as hazardous waste (Environment Agency 2008). Others, however, have concluded that, for the most part, there is still insufficient evidence to invoke the precautionary principle (Aitken et al. 2009; Stebbing 2009), and, hence, this issue may quite possibly take many years to resolve.

Current and near-future research effort distributions

In order to gauge whether current NM risk research efforts are responding to the challenges outlined above, we have undertaken a snapshot review of research efforts, mainly in terms of peer-reviewed journal publications, research projects and public funding within the fields of traditional risk assessment paradigms, complementary tools to risk assessment and risk governance mechanisms as they apply to NM. This is not intended to be a complete analysis of research publications and projects within the field of environment, health and safety aspects (EHS) of NM (see e.g. Aguar and Murcia Nicolás 2008; SCENIHR 2009 for more complete overviews); instead, we aim to provide a synopsis of the general direction and distribution of efforts to date.

We searched peer-reviewed journal articles within different nano-risk-related fields using the ISI Web of Knowledge article database ( and the International Council on Nanotechnology (ICON) database (‘quick’ and ‘advanced’ searches, which specifically focuses on EHS issues of NM. In addition, the OECD research project database ( which also specifically focuses on projects within health and environmental safety of NM was also searched. These databases were accessed and used on 30 June 2009. See Fig. 1 for more details on the search methodology, including search terms used.
Fig. 1

Comparison of number of journal article publications and research projects within different nano-risk topics and environment, health and safety (EHS) issues of nanomaterials (NM). The ISI Web of Knowledge ( and ICON Virtual Journal ( which specifically focuses on EHS issues of NM (using both ‘quick’ and ‘advanced’ search options) were used to search for scientific journal publications. The OECD NM risk research project database ( was used to search for completed or on-going research projects, shown on the secondary axis. Searches were made within all years in these databases, and were accessed and used on 30 June 2009. The following search terms were used within the ‘topic’ fields of the database search engines: ‘toxicity’, ‘ecotoxicity’, ‘exposure’, ‘risk assessment’, ‘risk management’, ‘risk governance’, ‘decision making’, ‘management’ and ‘monitoring’. Since the ISI Web of Knowledge database is not confined to NM risk research, as in the case of the ICON and OECD databases, the previously cited search terms were used together with ‘nanotechnology’, ‘nanomaterial’ or ‘nanoparticle’

In terms of the number of published research articles and research projects within different nano-risk fields, the majority (60.1%) of these research efforts were within the topics of ‘toxicity, ‘ecotoxicity’ and ‘exposure’ of NM (Fig. 1). There were also relatively high numbers of research articles found in topics of ‘management’ and ‘monitoring’ of nanotechnology, -material or -particle using the ISI Web of Knowledge, although the number of articles found within these topics is significantly less when using the ICON database which specifically focuses on EHS aspects of NM. In comparison, only 6.8 and 1.6% of research efforts were in the areas of ‘risk governance’ and ‘decision making’, respectively.

Similar patterns are also seen in the distribution of research projects completed or underway within NM EHS issues. According to the OECD project database for health and environmental safety research of NM, there were 153 projects listed under topics of ‘exposure’ and 99 projects within ‘toxicity’ or ‘ecotoxicity’, compared to 45 within ‘risk assessment’, 37 within ‘monitoring’, 16 within ‘management’ and 6 within ‘risk management’. Only two projects are within the field of ‘risk governance’ and three in the field of ‘decision making’ (Fig. 1).

It is evident, not unsurprisingly, that much of the ongoing research fits within a chemical-based risk assessment paradigm. Very little research is directly addressing the key issues of near-term decision support highlighted above and by others (RCEP 2008; Brown 2009; Linkov et al. 2009b).

Furthermore, this situation is not likely to change in the near future. Of the nearly 200 projects funded either through the EU Framework Programmes (totally € 32 million), EU Member States, Candidate Countries or Countries associated to Sixth Framework Programme (FP6) or Seventh Framework Programme (FP7) (totally € 47 million), only a few projects focus on risk governance or decision making (Aguar and Murcia Nicolás 2008). The great majority of projects have been dedicated towards improving technical knowledge or developing new test protocols and equipment. Similar patterns are seen in US public funding schemes through the National Nanotechnology Initiative (NNI 2008a, b). Funding schemes outlined by the EU’s current FP7 programme do not appear to deviate much from previous research priorities (Aguar and Murcia Nicolás 2008; European Commission 2009). The recent FP7 call, (Theme 4 Nanosciences, Nanotechnologies, Materials and New Production Technologies—NMP), published 29 July 2009, is aimed largely at gaining more technical knowledge for risk assessment (European Commission 2009). Very few references are made on improved governance or decision making of nanotechnologies, with no specific calls within these areas. These are largely subsumed within wider goals, such as improved social acceptance, sustainable development and the development of reference materials. This is not surprising given the overarching strategy outlined by the EU nanotechnologies action plan (European Commission 2005) which is yet to acknowledge the key issues raised in this article and by others (e.g. RCEP 2008).

Redressing the imbalance: a path forward and recommendations

This analysis has shown that despite the recognized serious challenges that NM present for fulfilling traditional chemical-based risk assessment frameworks and the time this will likely take, the large majority of decision support research is directed to fit ultimately within this framework. Decision makers, therefore, may not be well equipped to make decisions concerning NM under conditions of extensive uncertainty in relation to environmental and human health protection in the near term. It is clear, in our view, that there is a need for a program of research and knowledge transfer specifically aimed at supporting near- and medium-term decision making, in real time and at the same pace as nano-innovation itself (Guston and Sarewitz 2002), see Box 1. Furthermore, since there are already a number of NM on the market with varying degrees of potential for exposure (Limbach et al. 2008; RCEP 2008; SCENIHR 2009), we also recommend the use of environment and health surveillance as an early warning system to act as a safety net around such a decision support program, to which it may also serve to inform (Box 1). We have highlighted these areas that might be worthy of consideration in such a research program in Box 1 and provide further justification for these in the following section.
Box 1

In response to the challenges of potential health and environmental risk assessments of nanomaterials (NM) and making decisions regarding these potential risks, as highlighted in this analysis, we propose some key areas for future research to ensure the responsible emergence of nanotechnologies




Adaptive and more responsive risk governance frameworks

Rapid nanotechnologies innovation out-paces regulatory governance based on traditional risk assessment

Encourage and support research on risk governance which specifically focuses on timely yet informed decision making in light of uncertainty and rapid nano-innovation

Lengthy, post-innovation risk investigations

Integrate responsible innovation early (upstream) in innovation process

Alternative, complementary tools to risk assessment

Early approximate risk evaluations

Immediate, rigorous testing of already-developed tools to fully evaluate their functionality and limitations

Relative comparison of NM risks for decision support

Continue development of new tools including those which may complement risk assessment

Health and environmental surveillance

Early warning system

Use of biomonitoring, such as:

Potential safety net

 Filter-feeders in aquatic ‘hot spots’

 Monitor health of occupational workers

 Direct Toxicity Assessment of effluents

Adaptive and more responsive risk governance frameworks

If the development of regulation based on quantitative risk assessment is an inherently slow governance process, then one answer might be to undertake research that leads to one or more governance frameworks that are more responsive and adaptive. This is a view that has been articulated by a number of authors, including RCEP (2008), Brown (2009) and Owen et al. (2009a). There is a foundation for this study, including a number of alternative risk governance frameworks that have been proposed in recent years, such as those suggested by the International Risk Governance Council (IRGC 2007), Environmental Defense and Dupont (Nano Risk Framework, Environmental Defense and Dupont 2007) and SMARTEN (Strategic Management and Assessment of Risks and Toxicity of Engineered Nanomaterials) (Metcalfe et al. 2009). These typically not only combine some of the traditional parameters of risk assessment (hazard identification, exposure assessment, etc.) and risk management (in the case of the Nano Risk Framework), but may also incorporate wider aspects (e.g. social, economic and cultural aspects, expert analysis).

Others have proposed broader governance models for decision making of nanotechnology. For example, real-time technology assessment attempts to integrate nano-science and innovation with social science and policy at early stages of research and development rather than dealing with decision-making issues after innovation has already taken a place in society (Guston and Sarewitz 2002). This has the potential to prevent lengthy post-NM production debates by addressing key issues early in the innovation process, given that the inclusive steps involved are coordinated and well guided to minimize delay in the process. While real-time technology assessment mainly aims to assist decision-making processes by incorporating other (societal) factors, it is not yet clear if more timely decisions will ultimately be aided by this process.

Others have specifically recognised the key issue of driving governance ‘upstream’ in the nano-innovation process. For example, the European Commission’s Code of Conduct for Nanosciences and Nanotechnologies Research was established in 2007 (European Commission 2008a), providing guidance to steer the responsible development of nanotechnology at an early stage. This includes specific recommendations aimed towards enhancing communication of the risks, benefits and uncertainties in addition to the development of scientific tools and knowledge, albeit described, in general, rather than in specific terms.

In short, while there are a number of potential avenues to pursue, a comprehensive programme of research in this area is currently lacking. Therefore, we recommend the continued development of research on risk governance frameworks that specifically aims to strengthen the timeliness of decision making processes in the face of rapid nanotechnologies innovation.

Alternative, complementary tools to risk assessment

In addition to the risk governance frameworks and approaches described above, a wide variety of tools have either been developed or deployed for approximate risk evaluations or decision making about (some) NM risks using available information. These include the Precautionary Matrix to identify potentially dangerous applications within production (Höck et al. 2008) and a categorisation framework to identify different exposure potentials based on the location of the nano-structured material in a product (Hansen et al. 2008). Multi-Criteria Decision Analysis (MCDA) and SMAA–TRI models have also been proposed, which compare and rank alternatives in NM risk decision making (Linkov et al. 2007; Tervonen et al. 2009). Furthermore, expert elicitation has been put forth to help compensate for large data gaps (Morgan 2005), as well as adaptive management to help create flexible and iterative processes (Davis 2007; Linkov et al. 2007). In general, these tools attempt to provide either an early attempt to approximate or compare some NM risks for decision support, even if it is, for example ranking the risks of different nanoparticles.

While these tools and models may be valuable in many aspects, especially in terms of ‘thinking outside the box’ in regard to early estimates and comparisons of NM risks and better decision-making strategies, one main limitation is that many (if not most) of these tools and models have not been thoroughly ‘tested’ and applied to many NM, and, therefore, their robustness and applicability is not yet clear. Therefore, we recommend that the developed frameworks and tools, some of which have been described here, be immediately and rigorously tested to fully evaluate their functionality and limitations. This should be complementary to the continued development and amendment of alternative governance frameworks and tools.

The need for surveillance

Since decisions under uncertainty and especially ignorance will always be prone to varying degrees of error, some have suggested the need for ‘corrigibility’ (Collingridge 1980). In other words, under uncertain circumstances, it is important to ensure that such decisions can be reversed at minimum cost (economic or otherwise). Hence, environmental and health surveillance may have the potential to serve as an important safety net or early warning system (Owen et al. 2009b; Saunders and Mohammed 2009; Schulte et al. 2009) to any decision support system for NM risks, whether based on prospective risk assessment or an alternate framework. In particular, the use of biomonitoring may be particularly useful given the difficulties in detecting and measuring nanoparticles in complex environmental matrices (e.g. Hassellov et al. 2008). This might include evaluating the toxicity of NM-containing environmental discharges (e.g. ‘whole effluent assessment’ or ‘direct toxicity assessment’, Owen et al. 2009b) or the use of filter feeding organisms in aquatic environments where there is an anticipated high degree of exposure to NM (Baun et al. 2009). Biomonitoring may also encompass the monitoring and surveillance of occupational workers’ health in the light of potentially hazardous effects of NM (Nasterlack et al. 2008). In fact, the National Institute of Occupational Health and Safety (NIOSH) recently recommended hazard surveillance as a foundation to implement safety measures (NIOSH 2009), and the OECD has recommended the inclusion of health monitoring, surveillance and biological monitoring for occupational workers (OECD 2009c).


Although the traditional chemical-based risk assessment framework is a powerful approach, its use for estimating the health and environmental risks of NM in the near-term may be limited due to the time and costs needed to generate meaningful results. This is due to the extensive risk uncertainties and complex types and numbers of NM encountered in current production. The fast-paced development of NM and nanoproducts is only compounding this problem. Given these limitations, decision makers may not currently be well equipped if decisions are to be based mainly upon results generated from quantitative risk assessment. We see this as the central issue for the responsible emergence of nanotechnologies.

Despite the above, research efforts thus far have been mainly put towards acquiring knowledge that will most likely be fed into chemical-based risk assessment procedures. These efforts include a predominance of research publications and projects within the fields of (eco)toxicology and human and environmental exposure of NM, while research in broader issues such as decision making and risk governance are comparatively minimal. Research supporting quantitative risk characterization of NM is indeed important, and we do not advocate abandonment of this at any cost. However, as scientists and policy makers, we must face the reality that knowledge gaps are not expected to be closed in the near future and may take decades to close in many cases. In order to ensure the protection of the environment and human health, this suggests the need for a research programme as significant as that which feeds into quantitative risk assessment and which addresses the fundamental issue of timely, yet, informed decision making regarding potential NM risks. Although a few alternative risk frameworks have been proposed, it is not clear whether they will address this key concern. Furthermore, although some complementary governance approaches and decision support tools have been suggested, their comprehensive evaluation and development has yet to be undertaken.

In conclusion, we suggest the need for an international research programme that specifically addresses critical issues of risk governance and timely decision making as these relate to NM specifically, and emerging technologies more generally. This programme might include research into more efficient and anticipatory risk governance mechanisms as well as a systematic evaluation of available complementary tools to risk assessment and, where necessary, further tools under development. Finally, the development of environmental and health surveillance is needed to act as a safety net and an early warning system while these issues are being addressed. We recommend that active research within these areas should be among the essential steps taken in the near future to ensure the responsible emergence of nanotechnologies, and ultimately the protection of human and environmental health.


Defined according to Renn (2008): “Risk governance includes the totality of actors, rules, conventions, processes and mechanisms concerned with how relevant risk information is collected, analysed and communicated, and how management decisions are taken”.


As described by the European Commission (2000).


Copyright information

© Springer Science+Business Media B.V. 2009

Authors and Affiliations

  1. 1.Department of Environmental EngineeringTechnical University of DenmarkKongens LyngbyDenmark
  2. 2.Policy Studies InstituteLondonUK