Internationally, there are efforts to develop standardised toxicity testing and risk assessment methods for engineered nanomaterials (ENMs). To this end, health risk
assessments need to be conducted on ENMs synthesised in South Africa. Country-specific risk characterisation requires specific exposure assessments for those ENMs for
which the likelihood exists for occupational and environmental exposure in that country. A challenge in hazard identification and risk assessment related to ENMs,
regardless of country of origin, is that data on toxicity, carcinogenicity, pharmacokinetics, and occupational or environmental exposure are generally not available for
most ENMs. Although the mechanisms previously identified as important in the toxicity and carcinogenicity of particles and fibres may be applicable, the possibility
exists that the unusual physicochemical properties of ENMs may give rise to unique, and as yet unidentified, adverse effects. Moreover, generalised exposure scenarios
that consider the life cycle of the agent have not been developed and are needed for the complete risk characterisation of ENMs. As health risk assessment is both
resource and labour intensive, it is imperative to identify the aims of such an exercise prior to embarking on large-scale projects, to ensure that the data most useful
for public health decision-making is provided. Identifying priorities in South Africa, in coordination with international efforts, can facilitate the effective use of
research efforts for risk assessment and risk management decision-making.
Health risk assessments are required for new technologies and for new classes of materials introduced to the market for human use. Amongst the most extensive regulation
in this area is the European Union Registration, Evaluation, Authorisation and Restriction of Chemicals (REACH) programme.1 Risk assessment
on categories of nanomaterials have been proposed, with consideration given to their physicochemical properties and modes of
action.2,3 These categories are:
carbon-based (fullerenes and carbon nanotubes), metal-based (quantum dots, nanogold, nanosilver and metal oxides), dendrimers and
It is anticipated that workers and researchers handling these diverse engineered nanomaterials (ENMs), as well as the general public that use these products, will to
some degree be exposed to, and therefore potentially at risk from, their adverse effects.6 Agencies and organisations in several countries
guidelines on good work and consumer practices for the handling and use of ENMs,2,7,8 and have
formulated approaches for the evaluation of ENMs under
existing health and safety regulations.5
A global effort to develop standardised testing procedures for risk assessment is led by the Organization for Economic Cooperation and Development (OECD). A list of
priority ENMs has been developed and country sponsors have been identified9 (Table 1). South Africa is the sponsor for the most recent
addition to this list,
gold nanoparticles (AuNP); the USA is a co-sponsor, and the European Commission (EC) and Korea are contributors. The OECD standardised testing procedures include
information on physicochemical characterisation, biotic systems, degradation and accumulation, and health effects.10 Phase I testing
(introduced in 2007)
includes the selection of the ENMs and the end points to be studied (Table 2). Phase II involves the evaluation of critical issues identified in Phase I or the
performance of additional tests, including long-term tests and risk assessment. Data sharing of the tested ENMs will increase the efficiency of generating data
needed for hazard and risk assessment.10
TABLE 1: List of nanomaterials and their country sponsors for toxicity testing.
TABLE 2: List of end points to be studied in Phase I of the country-sponsored testing programme.
The Department of Science and Technology (DST) in South Africa has also emphasised the need for risk assessment of ENMs presently synthesised in the
country.11 Without reliable data on effects and exposure, in-depth risk assessments of ENMs in South Africa and other countries
may be limited. It is
therefore essential to coordinate international efforts and develop standardised methods for in-vitro and in-vivo hazard identification to provide data
for the risk assessment of representative ENMs within major categories. The purposes of this review are to, (1) provide an overview of risk assessment history and
practice, (2) describe coordinated international research efforts in which South Africa participates and (3) discuss challenges in health risk assessment and areas of
prioritisation for South Africa.
Overview of health risk assessment of nanomaterials
The objective of human health risk assessment is to provide scientific information based on toxicology or epidemiology data (if available) to predict or estimate risk
associated with exposure to potentially hazardous substances. Traditionally, health risk assessment involves four steps (proposed in 1983 by the US National Research
Council)12: (1) hazard identification, (2) dose–response assessment, (3) exposure assessment and (4) risk characterisation
(Figure 1). Throughout each
step of this process, uncertainties involved in making estimates also need to be considered.4,13
Examples of the use of risk assessment for risk management decision-making include regulatory measures for establishing standards for water and air quality or
requirements for environmental clean-up. Through the identification of potential sources and pathways of exposure for a population, and the determination of the health
hazards associated with exposure, risk characterisation describes the potential risk of a substance, from those that present little or no concern, to those that are
likely to cause adverse effects. Risk assessment supports evidence-based risk management decisions and facilitates societal evaluation of acceptable
Basically, it is anticipated that the risk assessment of ENMs will follow the traditional risk assessment paradigm used for conventional
Nanoparticle-specific data are also needed in applying the risk assessment process and to determine if there are any novel properties of nanomaterials that may result
in unique toxicity. New strategies and methods may be needed to identify and consider any factors that may be specific to
FIGURE 1: The health risk assessment paradigm.
The first step in risk assessment is to evaluate the available hazard data, including that of in-vitro or in-vivo toxicity. The purpose of hazard
identification is to identify the contaminants that may pose health hazards and to identify the conditions under which they could be toxic to
The potential hazards of a great number of ENMs have as yet not been identified. Numerous past investigations of inhaled particles and fibres have identified properties
that determine toxicity as well as the mechanisms involved in this toxicity. For example, some physicochemical properties identified are chemical composition, particle
and fibre geometry and dimensions, biopersistence, surface activity and dose (as particle surface area, number, mass or volume). Mechanisms elucidated in particle and
fibre toxicity include oxidative stress and persistent inflammation.6 It is therefore envisaged that similar mechanisms may be applicable
to the potential toxicity of ENMs.
With the help of expert groups, a number of international agencies have proposed specific in-vitro and in-vivo tests to assess the toxicity of
ENMs.10 In-vitro assays are considered useful for screening and prioritising substances for in-vivo studies. Such assays
may also be useful in
the elucidation of the mechanistic pathways involved in the toxicity of nanomaterials, which may need further validation with in-vivo studies. Some recent studies
have shown progress in correlating acute in-vivo and in-vitro responses in hazard identification,6 which suggest
that in-vitro assays
could be used to reduce animal testing in the initial hazard evaluation of ENMs.
Internal dose estimation is important in the prediction of the biological effect at the target tissue (based on absorption, distribution, metabolism, and elimination
processes). Although data still are limited, the role of physicochemical properties on the systemic distribution of some ENMs, including AuNP, has been studied.
In-vivo studies have shown that the primary site of gold (and silver) accumulation is the liver,17 and that this process of
accumulation is influenced
by particle size, surface charge and route of exposure.18 For example, in a rat intratracheal instillation study of two sizes of
AuNP, the pulmonary and
systemic toxicity responses were similar for both particle sizes at the dose tested, and there was no clear relationship between toxicity and particle size or
agglomeration state.19 A subchronic inhalation study of exposure to AuNP in rats showed no adverse effects in rats exposed to the two lower doses, but rats
exposed to the highest dose showed reduced lung function and inflammatory changes in their lung tissue.20 Further studies are needed to
assess the hazards of
AuNP, although in-vivo and in-vitro studies suggest that particle size and charge can influence the fate of gold nanoparticles in the body. For
other materials, particle shape also influences the ability of inhaled particles to translocate from the lungs and be retained in the pleural tissue. Such kinetic
information can be used to identify the nanomaterial characteristics with the greatest potential to be hazardous and to design nanomaterials with safer properties
(e.g. lower biopersistence).21
The next step of the risk assessment process is the dose–response assessment, in which the quantitative relationship between the dose and a toxic response is
determined. This assessment is typically performed using animal models, from which an equivalent human dose (often for a specific population, such as workers or the
general public) is estimated.12
The aim of this step is to identify the doses at which certain toxicity end points (i.e. effect levels) occur. These end points can include acute and chronic toxicity,
immunotoxicity, neurotoxicity, mutagenicity, reproductive or developmental toxicity, and carcinogenicity. Another aim of this step is to identify the effect level, such
as the ‘no observed adverse effect level’ (NOAEL) or the ‘lowest observed adverse effect level’ (LOAEL). Non-cancer risk assessment using a NOAEL
or LOAEL approach assumes a threshold mechanism such that exposures below the threshold are not expected to cause harmful effects. The most sensitive end point is
typically selected and extrapolated to humans by adjusting for differences across species (e.g. body weight and metabolic rate). The human-equivalent effect level is
then divided by a series of uncertainty factors to determine a reasonably safe exposure level. Uncertainty factors are typically those that account for a less than or
equal to 10-fold difference caused by species differences, animal vs. human response, human inter-individual variability, use of a LOAEL instead of a NOAEL and use of
subchronic rather than chronic dose–response data. Examples of regulatory levels derived using this approach include inhalation reference concentrations (RfC),
oral reference doses (RfD) and acceptable daily intakes (ADI).22 Alternatively, risk-based effect levels can be estimated from
statistical modelling of the
dose–response data and low-dose extrapolation from the 95% lower confidence limit estimate (i.e. the benchmark dose limit, BMDL) of the benchmark dose (BMD). The
BMDL is used to account for variability in the data and to provide confidence that the true BMD is greater than the BMDL. The US National Research Council risk
guidelines recommend a greater emphasis on risk-based approaches to decision-making, such as in the development of exposure limits and reference
There are two major issues that are of concern when establishing the dose–response relationship of ENMs. Firstly, challenges exist in the measurement of
nanoparticles at target deposition sites and their biopersistence at those sites. A number of physicochemical properties, including their surface functional groups and
dissolution of surface ions, may influence their distribution to these sites.23 Secondly, the establishment of the most biologically
relevant dose metric for
nanoparticles (mass, volume, number or surface area) poses a further challenge in the establishment of a dose–response relationship
for ENMs.24 Particle
volume or surface area, rather than mass, have been shown to better describe the overloading of lung clearance and the resulting inflammation response in
rats.25,26 A recent study has concluded that no single dosimetric parameter of particles – mass,
surface area or number – will be universally
applicable to all nanomaterials. Hence, the selection of the best dose metric for toxicity testing and the risk assessment of specific ENMs will remain a
challenge.27 Toxicity studies can help to reduce this challenge by providing standard measures of physicochemical properties at
toxicity to facilitate
hypothesis testing across groups of ENMs.
Obviously, there is no risk to health from a hazardous agent if there is no exposure to that agent. Exposure assessment identifies the exposure of a population to a
contaminant, and includes the route, magnitude, duration and timing of the exposure.12
Exposure assessment may cover medical administration through intradermal, intraperitoneal and intravenous injections.28 Exposure may also
be in the form of
inhalation, ingestion and dermal absorption in occupational settings. In addition, exposure through the general environment, the fate and transport of the substance, as
well as the points of entry into the environment or through the use of consumer items, should be considered.
Adequate exposure assessment cannot be conducted without sufficient information on the sources of exposure, the amount exposed to and the routes of exposure. Exposure
via inhalation is possible for airborne nanomaterials; exposure via the gastrointestinal tract is possible because of the increasing number of applications of ENMs in
food packaging and food products. Workers are at risk from dermal exposure to ENMs during the manufacture of ENMs. Workers and the general public are also at risk from
dermal exposure to ENMs through the manufacture and use of textiles and cosmetics such as sunscreens. Because of lack of data on ENMs in the aquatic or terrestrial
environment,29 it is even more challenging to estimate exposure of the general population or the environment to ENMs. Once again,
the unique physicochemical
properties of nanomaterials may determine their behaviour in different environments and therefore their frequency or patterns of exposure.
Finally, exposure varies on the basis of conditions such as the manner in which materials are handled in the workplace, the way in which ENMs partition to various
phases (e.g. water and air), and the mobility and persistence of ENMs in each of these phases, and the magnitude of the sources (e.g. production volume or size of
markets). Exposure scenarios for the identified ENMs should therefore be developed throughout their life cycles to address key questions and gaps in the risk assessments
of the identified ENMs. It may be likely that when an ENM is embedded in polymers or in other materials, the potential for exposure is
minimal,30 but this
potential may change during the processing or recycling of the material, or as it enters a waste stream. In this instance, the life-cycle concept propagated by the
Environmental Protection Agency should also be considered for the risk assessment of nanoparticles.31
The final step in risk assessment is risk characterisation, in which data obtained during hazard identification, dose–response assessment and exposure assessment
are integrated, and the uncertainty in these estimates is evaluated.13
The paucity of data for many ENMs with regard to workplace exposure levels and hazard potential are key sources of uncertainty in the risk characterisation of these
ENMs. There is also uncertainty about the potential novel or enhanced effects of certain ENMs as a result of their small size and their ability to interact with cells
and cell organelles via mechanisms related to nanoscale properties. Additional uncertainties include the influence of the route of exposure (e.g. inhalation via air,
ingestion via food or water or intravenous via medical treatment) on internal dose and toxicity; the role of particle size (e.g. agglomerated versus dispersed); the
mechanisms involved in the uptake and fate of ENMs in the body; and the persistence or degradation of ENMs in the environment. A full life-cycle risk characterisation
would include not only the risk assessment of workers at the site of production, but also a risk assessment along the life cycle of the ENMs, including their transport,
use and disposal.31,32
The research efforts to address these questions are by nature multidisciplinary. Best work practice calls for greater exposure control and caution when there is
increased uncertainty about potential adverse health effects.33 In the absence of information on specific ENMs, the scientific
literature on substances
with analogous physicochemical properties could be used to derive initial estimates of the hazard and the target level of exposure
Examples of risk assessments and exposure limits for nanomaterials
The occupational exposure limits (OELs) currently proposed for ENMs are based on animal data, as human health effects data are not available for specific ENMs. The US
National Institute of Occupational Safety and Health used quantitative risk assessment methods similar to those used for other airborne, poorly soluble
particles34 as the basis for developing draft OELs for ultrafine (of nanometre diameter) and fine (of micrometre diameter)
Epidemiology studies of workers who handle TiO2 have generally shown no increase in the risk for lung cancer. Chronic inhalation studies in rats, however,
have shown an increase in the risk for lung tumours; this risk is associated with the particle surface area dose of TiO2 and other poorly soluble particles
in the lungs.35,36 Subchronic inhalation studies have shown that pulmonary inflammation is also associated with the
particle surface area dose in the lungs
of rats and mice. Because ultrafine TiO2 has a greater surface area per unit mass than fine TiO2, a lower mass dose of ultrafine TiO2
than that of fine TiO2 was associated with lung inflammation and tumours. These findings of adverse lung effects being associated with the particle size or
surface area provided the health basis for the two OELs proposed for fine and ultrafine (or nano) TiO2: 0.3 mg/m3 for ultrafine TiO2
and 2.4 mg/m3 for fine TiO2 (8-h time-weighted average concentrations).35
Several research groups recently have proposed specific OELs for carbon nanotubes (CNTs): 50 µg/m3,37
30 µg/m3,38 7 µg/m3,39 1–2 µg/m3.
proposed OELs are 8-h
time-weighted average concentrations and were derived from animal studies in which lung inflammation or fibrotic responses were exhibited after subchronic or short-term
exposure to different types of CNTs. Most of these risk assessments used data from subchronic inhalation studies of multiwalled CNTs in rats, in
which 0.1 mg/m3 was the NOAEL in one study38 and a LOAEL in a study of a different type of
multiwalled CNT.41 Another risk
assessment used data from a 4-week inhalation study in rats, in which the LOAEL was 0.37 mg/m3.37
Although these examples show progress in the development of proposed OELs for ENMs, the number of different types of nanoparticles being developed and used in commercial
products is outpacing efforts to develop OELs in the workplace. Reasons for this shortcoming include limited data on both the hazards of and the exposure to ENMs, for
example, in workplaces.42 Challenges in the measurement of exposure include the current inability of the available online monitoring
separate the ubiquitous background nanomaterials from the ENMs; limitations in the sensitivity of some analytical methods for detecting and quantifying exposures to
nanoparticles in the workplace39; and the lack of consensus on the metrics and methods to be used for exposure
measurement.4,16 Thus, new
approaches are needed to better characterise potential hazards.
The concept of developing exposure limits for categories of ENMs with similar physicochemical properties – and well-characterised biological effects for
representative ‘benchmark’ particles in each group – may be one approach to setting exposure limits for different types of
The British Standards Institute proposed four categories of ENMs and associated ‘benchmark exposure levels’, which were described as pragmatic guidance
levels.2 A four-category approach was also adopted by the Institut für Arbeitsschutz43 in Germany.
Standardised toxicity testing procedures
and risk assessment methods are also needed for global harmonisation of health and safety practices for ENMs.10,32
Nanomaterials currently synthesised in South Africa
With the realisation of the importance of nanotechnology, and the foresight and leadership of the DST, centres dedicated to the research and development of nanotechnology
have been established to research the synthesis and applications of nanomaterials.44 Tertiary institutions (the universities of the
Witwatersrand, Cape Town,
Tshwane, Johannesburg, Stellenbosch, Western Cape, Zululand, KwaZulu-Natal, Limpopo and Rhodes) and research centres (the Council for Scientific and Industrial Research,
MINTEK and iThemba Laboratory for Accelerator Based Sciences) in South Africa are presently actively involved in the synthesis and application of nanomaterials.
Nanomaterials that are currently being investigated at these centres range from metal and metal oxide particles to CNTs and nanocomposites, and thus represent some of the
major categories of ENMs being developed and used worldwide (Table 3). A few examples of these activities, by no means an exhaustive list, are summarised below as an
indication of the diversity of nanomaterials investigated in South Africa.
List of nanotechnology-associated activities and materials in South African tertiary and scientific institutions.
AuNPs are being investigated for use in catalysis,45 in the purification of air at room temperature46
and in molecular
Almost every university and research centre is in some way involved with the synthesis or application of CNTs. The application of CNTs in
catalysis48 and their
use in the removal of hexavalent chromium from industrial wastes49 have been reported. These ENMs are also being studied for their
potential to cheaply and
efficiently treat water in order to meet drinking, industrial and environmental water quality standards.50
In South Africa, quantum dots and their application in diagnostics, security systems, biological probes and optics are being
investigated.51 A great variety
of nanocomposites is also being synthesised, including CNTs, polymers, quantum dots and metallic-based nanoparticles such as
silicon and TiO2.52
Finally, the preparation of magnetite nanoparticles, using a variety of synthesis methodologies,53 with anticipated applications for
therapeutic and diagnostic testing and densimetric separation, is being undertaken.
The complexity of understanding the potential exposure and toxicity of so many variations of ENMs is illustrated by the variety of compositions and applications.
Determining which materials are most likely to result in exposure, prioritising materials for specific testing, and determining to what extent physicochemical properties
can be used to infer hazard, are some of the challenges in the risk assessment of ENMs. Protecting researchers and workers who are producing and using these materials is
paramount, starting from the research laboratory and production line to the use of these materials in various applications.
Challenges in health risk assessment: Relevance to South Africa
The general consensus is that considerable work remains to be done to generate the required data for ensuring appropriate risk evaluation of ENMs. These data may include
the characterisation of the wide range of nanomaterials being produced and information on their complex behaviours in different media. Because of the diversity of ENMs,
toxicity is specific to a tested nanomaterial and cannot be generalised or extrapolated, even within the same chemical family. Not much is known about the
dose–response curves and toxicological modes of action of specific nanomaterials and how these materials might enter the body. Once inside the cell, the data
needed for specific ENMs, such as toxicity and carcinogenicity, adsorption, distribution, metabolism and excretion, as well as occupational and environmental monitoring
information, is largely unavailable. Moreover, longer-term effects of ENM need urgently to be addressed. Generalised exposure scenarios have also not been developed for
ENMs for risk assessment along the life cycle of an ENM.4 Without reliable data on effects and exposure, in-depth risk assessments of
ENMs for developing
risk-based management strategies or regulations cannot be conducted.
There is no methodical data available on nanomaterial production levels, on exposure scenarios in working environments or research laboratories, or on exposures
related to consumer products. Not much is known about emissions from nanomaterial production facilities and the fates of these emissions in the environment. In the
absence of adequate data, extra precautions in controlling exposure to ENMs are recommended.33
The development of a risk assessment for ENMs in South Africa is fraught with similar challenges as those experienced internationally. ENMs synthesised in many
countries, including South Africa, encompass a multitude of classes, which contain different subclasses and countless modified versions. Their diversity makes it
unfeasible to conduct an ad-hoc risk assessment of every type of nanoparticle. Thus the development of risk assessment strategies based on categories of
ENMs (e.g. based on mode of action) is needed.3 For ENMs to present a risk there must be both a potential for exposure and a hazard
from such exposure.
Prioritisation strategies for toxicity testing and risk assessment therefore consider which ENMs have the most commercial production and exposure
potential54; these priority ENMs may also vary by country.
Exposure and response data obtained from animals or humans, as well as information on sources of exposure and the physicochemical properties of the ENMs along their
life cycle are required for those ENMs identified as high priority for a comprehensive risk assessment. A tiered toxicity testing approach, that provides reliable and
predictive evidence of ENM-related toxicity or safety would be extremely important to support the appropriate testing of safety and toxicity of these
materials.4,10 Such an approach would allow one to separate materials of concern from those of lesser or no concern.
collaborators55 have developed a decision tree approach that incorporates tiered toxicity testing strategies. Another more comprehensive
strategy for ENMs has recently been proposed56 (Figure 2). The key issue in these approaches is well-defined decision points at which
testing can be
stopped or continued in a subsequent, more resource-intensive tier. Toxicity testing of ENMs should be initiated with a careful physicochemical characterisation of the
materials (Figure 2), including the use of reference materials currently available as dispersions,
especially for in-vitro studies.57
These well-characterised ENMs can then be further investigated in the next tier by first using acellular systems to explore the reactivity of the materials, before
exploration at a subcellular level. It would then be possible to proceed to in-vitro cellular models that would support evidence-based testing
processes.58 Such in-vitro testing methods should address carefully chosen and relevant end points shown to be predictive of human
toxicity.59 Positive and consistent results from validated in-vitro tests with demonstrated predictive power would lead to
higher tier testing
procedures with experimental animals. The advantages of this tiered system is that these lower tier tests would be short-term studies, and although long-term
studies with experimental animals would be required, these would be less frequently required than is the case today. A major challenge for the development of this kind
of tiered testing procedure continues to be the validation of in-vitro tests with appropriate predictive power for in-vivo effects in whole organisms,
although some progress has been shown for prediction of acute lung effects from in-vitro data.6,60
FIGURE 2: Proposal for toxicity testing strategy for engineered nanomaterials.
Risk assessment is the process of determining whether exposure to a substance will lead to negative health effects. A comprehensive risk assessment of ENMs will therefore
involve evaluation of the exposure potential, the hazardous properties and the dose–response relationship of ENMs. These findings could then be used to characterise
the risk and to provide information for risk-based decision-making, such as establishing exposure limits and other risk management measures to protect human health and
the environment – the ultimate goal of the risk assessment exercise.
For a resource-limited country such as South Africa, it is essential that best practice guidelines developed internationally be adopted and that research be conducted
as a priority to provide the data needed for risk assessments specific to the situation in South Africa.
We acknowledge the support of the Department of Science and Technology, South Africa and its initiative towards research on the risk assessment of nanomaterials.
We declare that we have no financial or personal relationships which may have inappropriately influenced us in writing this paper.
M.G. was the project leader and wrote the first draft of the article. E.D.K. and K.S. contributed sections as per their expertise in risk assessment and assisted in
finalising the article.
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