Review September 2012 | Volume 120 | Issue 9
Pharmaceuticals and Personal Care Products in the Environment: What Are the Big Questions?
Alistair B.A. Boxall,1 Murray A. Rudd,1 Bryan W. Brooks,2 Daniel J. Caldwell,3 Kyungho Choi,4 Silke Hickmann,5 Elizabeth Innes,6 Kim Ostapyk,6 Jane P. Staveley,7 Tim Verslycke,8 Gerald T. Ankley,9 Karen F. Beazley,10 Scott E. Belanger,11 Jason P. Berninger,2 Pedro Carriquiriborde,12 Anja Coors,13 Paul C. DeLeo,14 Scott D. Dyer,11 Jon F. Ericson,15 François Gagné,16 John P. Giesy,17 Todd Gouin,18 Lars Hallstrom,19 Maja V. Karlsson,1 D. G. Joakim Larsson,20 James M. Lazorchak,21 Frank Mastrocco,15 Alison McLaughlin,6 Mark E. McMaster,22 Roger D. Meyerhoff,23 Roberta Moore,6 Joanne L. Parrott,22 Jason R. Snape,24 Richard Murray-Smith,24 Mark R. Servos,25 Paul K. Sibley,26 Jürg Oliver Straub,27 Nora D. Szabo,28 Edward Topp,29 Gerald R. Tetreault,25 Vance L. Trudeau,28 and Glen Van Der Kraak26
Background: Over the past 10–15 years, a substantial amount of work has been done by the scientific, regulatory, and business communities to elucidate the effects and risks of pharmaceuticals and personal care products (PPCPs) in the environment.
Objective: This review was undertaken to identify key outstanding issues regarding the effects of PPCPs on human and ecological health in order to ensure that future resources will be focused on the most important areas.
Data sources: To better understand and manage the risks of PPCPs in the environment, we used the “key question” approach to identify the principle issues that need to be addressed. Initially, questions were solicited from academic, government, and business communities around the world. A list of 101 questions was then discussed at an international expert workshop, and a top-20 list was developed. Following the workshop, workshop attendees ranked the 20 questions by importance.
Data synthesis: The top 20 priority questions fell into seven categories: a) prioritization of substances for assessment, b) pathways of exposure, c) bioavailability and uptake, d) effects characterization, e) risk and relative risk, f ) antibiotic resistance, and g) risk management.
Conclusions: A large body of information is now available on PPCPs in the environment. This exercise prioritized the most critical questions to aid in development of future research programs on the topic.
Citation: Boxall AB, Rudd MA, Brooks BW, Caldwell DJ, Choi K, Hickmann S, Innes E, Ostapyk K, Staveley JP, Verslycke T, Ankley GT, Beazley KF, Belanger SE, Berninger JP, Carriquiriborde P, Coors A, DeLeo PC, Dyer SD, Ericson JF, Gagné F, Giesy JP, Gouin T, Hallstrom L, Karlsson MV, Larsson DG, Lazorchak JM, Mastrocco F, McLaughlin A, McMaster ME, Meyerhoff RD, Moore R, Parrott JL, Snape JR, Murray-Smith R, Servos MR, Sibley PK, Straub JO, Szabo ND, Topp E, Tetreault GR, Trudeau VL, Van Der Kraak G. 2012. Pharmaceuticals and Personal Care Products in the Environment: What Are the Big Questions? Environ Health Perspect 120:1221–1229; http://dx.doi.org/10.1289/ehp.1104477
Address correspondence to A.B.A. Boxall, Environment Department, University of York, York, YO10 5DD, UK. Telephone: 44 1904 434791. Fax: 44 1904 432998. E-mail: Alistair.firstname.lastname@example.org
We acknowledge participants in two related workshops performed in Korea and Australia. We are grateful to three reviewers who provided constructive comments on earlier versions of this paper.
AstraZeneca, Jannsen Pharmaceutical Companies of Johnson & Johnson, the American Cleaning Institute, and Health Canada provided financial support for the workshop. A.B.A.B.’s input to the project was partly supported by the U.K. Department of Environment, Food and Rural Affairs.
A.B.A.B., J.P.S., T.V., A.C., and P.C.D. have provided consultancy services to the pharmaceutical and personal care product (PPCP) industry. D.J.C., J.P.S., S.E.B., S.D.D., J.F.E., T.G., F.M., R.D.M., R.M.S., and J.O.S. are employed by the PPCP sector. A.B.A.B., B.W.B., K.C., J.P.S., T.V., A.C., P.C.D., F.G., J.P.G., M.V.K., D.G., J.L., J.M.L., J.L.P., M.E.M., M.R.S., P.K.S., E.T., G.R.T. V.L.T., and G.V., D.K. have received funding from industry and/or government for research on PPCP issues. M.A.R., D.J.C., S.E.B., P.C.D., F.M., R.D.M., J.R.S., and R.M.S. have shareholdings in the PPCP sector. S.H., E.I., K.O., G.T.A., K.F.B., J.P.B., P.C., L.H., A.M., R.M., and N.D.S. declare they have no actual or potential competing financial interests.
Received: 12 September 2011
Accepted: 18 May 2012
Advance Publication: 30 May 2012
Final Publication: 1 September 2012
- Supplemental Material (492 KB) PDF
Pharmaceuticals and personal care products (PPCPs) include numerous chemical classes. Pharmaceuticals are used primarily to prevent or treat human and animal disease, whereas personal care products are used to improve the quality of daily life and include products such as moisturizers, lipsticks, shampoos, hair colors, deodorants, and toothpastes. Human-use PPCPs are generally excreted and emitted into the sewerage system following use. The compounds may then be released into surface waters or enter terrestrial systems when sewage effluent is used for irrigation or where sewage sludge is applied as a fertilizer to agricultural land (Kinney et al. 2006; Ternes et al. 2004). Veterinary pharmaceuticals are released to the environment either directly, from use in aquaculture and the treatment of pasture animals, or indirectly during the land application of manure and slurry from livestock facilities (Boxall et al. 2003a). PPCPs may also be released to the environment from manufacturing sites (Fick et al. 2009).
PPCPs have been detected in the natural environment across the world (e.g., Hirsch et. al. 1999; Kolpin et al. 2002; Ramirez et al. 2009). Although reported concentrations are generally low, many PPCPs have been detected in a variety of hydrological, climatic, and land-use settings and some can persist in the environment for months to years (e.g., Monteiro and Boxall 2009). Pharmaceuticals, as well as several chemicals used in personal care products, are biologically active compounds that are designed to interact with specific pathways and processes in target humans and animals. Concerns have therefore been raised about the potential effects of active PPCPs in the environment on human and environmental health; over the past 15 years, a substantial amount of work has been done to determine the occurrence, fate, effects, and risks of PPCPs in the environment. Regulations have also been developed regarding the assessment of risks of environmental exposure to PPCPs [e.g., Center for Drug Evaluation and Research (CDER) 1998; Committee for Medicinal Products for Human Use (CHMP) 2006; Committee for Medicinal Products for Veterinary Use (CVMP) 2000, 2004; European Centre for Ecotoxicology and Toxicology of Chemicals (ECETOC) 2008; World Health Organization (WHO) 2011].
Attempts have been made to synthesize the wealth of knowledge gained to date and to identify the remaining major research gaps and gaps in regulation [e.g., Knowledge and Need Assessment of Pharmaceutical Products in Environmental Waters (KNAPPE) 2008]. However, these exercises have tended to focus on select regions of the world, as well as established markets, and have not always engaged fully with major stakeholder groups.
One approach to identifying key issues in a topic area is to perform a “key question exercise, ” which is designed to promote engagement of researchers and stakeholders from a broad range of sectors (e.g., Fleishman et al. 2011; Rudd et al. 2011). The exercise begins with an initial solicitation of interested parties to develop a list of questions that individual members of the community feel are important regarding a particular topic. A workshop is then held to discuss and prioritize the questions raised and to develop a final list of questions (e.g., 20, 40, or 100). In this review we report the results of a key question exercise that was performed to identify and rank the top 20 questions related to the hazards, exposure assessment, and environmental and health risks of PPCPs in the natural environment. A description of the approach used, the submitted questions, and questions taken forward to the workshop is available in Supplemental Material, pp. 2–29 (http://dx.doi.org/10.1289/ehp.1104477).
Top 20 Questions
The top 20 questions fell into seven categories: a) prioritization of PPCPs, b) pathways of exposure, c) bioavailability and uptake, d) effects characterization, e) risk and relative risk, f ) antibiotic resistance, and g) risk management.
Prioritization of PPCPs
What approaches should be used to prioritize PPCPs for research on environmental and human health exposure and effects? More than 4, 000 pharmaceuticals are currently in use, and many types of chemicals are used in personal care products; it would be impossible to experimentally assess the hazards and risks of all of these in a timely manner. Prioritization approaches can be used to focus monitoring, testing, and research resources and to identify those PPCPs that are likely to pose the greatest risk in a particular situation. Several prioritization methods have been proposed for—and applied to—human pharmaceuticals (e.g., Kostich et al. 2010; Kostich and Lazorchak 2007; Sanderson et al. 2004) and veterinary medicines (Boxall et al. 2003b; Capelton et al. 2006; Kools et al. 2008). Many of these approaches use either exposure and toxicological predictions or information on pharmaceutical potency, so they can be readily applied to large numbers of compounds. These approaches should be further developed for different situations covering different geographical regions, climates, demographics, and cultural backgrounds and should be designed in such a way that they account for the use practices, complex fate processes, and the specific modes of action associated with many PPCPs.
Pathways of Exposure
What are the environmental exposure pathways for organisms (including humans) to PPCPs in the environment, and are any of these overlooked in current risk assessment approaches? PPCPs can enter the environment by a number of pathways (Figure 1). Regulatory environmental risk assessment approaches for PPCPs consider releases to surface waters from wastewater treatment systems, aquaculture facilities, and runoff from fields, as well as releases to soils during biosolid and manure application [e.g., CHMP 2006; CVMP 2008; Price et al. 2010]. Other exposure pathways exist, including emissions from manufacturing sites (Fick et al. 2009), disposal of unused medicines to landfills, runoff of veterinary medicines from hard surfaces in farmyards, irrigation with wastewater, off-label emissions, and disposal of carcasses of treated animals. Management and use practices in different regions of the world can also vary, so an important exposure pathway in one geographical area may be a less important pathway in another region. For example, in several regions of the world, the connectivity of the population to wastewater treatment technologies is limited, so regulatory exposure modeling based on European and North American systems will not always be relevant. An understanding of the release mechanisms and dominant exposure pathways for PPCPs in different regions is therefore needed.
Bioavailability and Uptake
How can the uptake of ionizable PPCPs into aquatic and terrestrial organisms and through food chains be predicted? A significant proportion of PPCPs are ionizable substances. Although methods are available for estimating uptake of ionizable compounds into fish and invertebrates (e.g., Fu et al. 2009; Meredith-Williams et al. 2012), our understanding of the factors and processes that influence uptake of PPCPs from different environmental compartments into organisms is still less well developed than for nonionizable chemicals (Brooks et al. 2009). The uptake of ionizable PPCPs is also very sensitive to changes in environmental conditions such as pH and soil and sediment characteristics. Data on uptake through food chains is almost nonexistent. Future work should therefore focus on understanding the uptake routes for PPCPs from a range of matrices into single organisms and food webs covering different traits (e.g., size, life cycle characteristics, method of respiration). Based on these studies, improved models should be developed for estimating uptake of ionizable PPCPs into organisms and through food chains.
What is the bioavailability of nonextractable residues of PPCPs? Many PPCPs dissipate rapidly in animal manure, biological treatment processes, soils, and sediments. Data from degradation studies with radiolabeled PPCPs indicate that, in many instances, the observed dissipation can be due to the formation of nonextractable residues (NERs; e.g., Kreuzig and Höltge 2005). NERs are species of a chemical that cannot be extracted from a matrix (sediment, soil, etc.) by methods that do not significantly change the chemical nature of the residues. In general, the chemical identities of these NERs are unknown. Concerns have been raised that, in the future, NERs may become bioavailable due to breakdown of manure and biosolid material added to soils, or due to changes in agricultural practices or the environment, such as changes in the pH or ionic strength of a system (Barraclough et al. 2005; Gevao et al. 2000). The challenge is to demonstrate whether NERs for PPCPs are bioavailable or whether they are likely to become bioavailable. This is a challenge not only for PPCP risk assessment but also for other classes of chemicals, including pesticides (e.g, Calderbank 1989; ECETOC 2010).
How can pharmaceutical preclinical and clinical information be used to assess the potential for adverse environmental impacts of pharmaceuticals? A lot of information is available from mammalian studies and clinical trials on the behavior and effects of active pharmaceutical ingredients. The pharmaceutical industry devotes significant resources to collating new and emerging data as part of their postauthorization pharmacovigilance programs, and several epidemiological studies have been performed to explore the potential long-term health effects of pharmaceuticals on workers in the pharmaceutical industry (e.g., Heron and Pickering 2003). In contrast, comprehensive information on fate and effects in the environment is publicly available for only a small percentage of pharmaceuticals and, with a few exceptions (e.g., the U.K. Veterinary Medicines Directorate Suspected Adverse Reactions Reporting Scheme), pharmacovigilance programs do not examine environmental effects. By accessing the wealth of data from mammalian studies and clinical trials and by building upon the advanced methods for predicting long-term, low-level effects arising from occupational exposure, it may be possible to establish whether low levels of a pharmaceutical in the environment constitute a threat to environmental and human health (Ankley et al. 2007; Berninger and Brooks 2010; Huggett et al. 2003; Seiler 2002).
What can be learned about the evolutionary conservation of PPCP targets across species and life stages in the context of potential adverse outcomes and effects? Most pharmaceuticals, and a few personal care products, are designed to interact with a target (such as a specific receptor, enzyme, or biological process) in humans and animals to deliver the desired therapeutic effect. If these targets are present in organisms in the natural environment, exposure to some PPCPs might be able to elicit effects in those organisms. Knowledge of the presence or absence of PPCP targets across a wide range of taxa could therefore be invaluable in identifying PPCPs that might affect the environment at low concentrations, and those organisms and life stages of organisms that are most likely to respond to exposure to a particular pharmaceutical (Ankley et al. 2007; ECETOC 2008; Gunnarsson et al. 2008; Huggett et al. 2003; Seiler 2002; Trudeau et al. 2005). Comparative biochemistry, genomics, and other “omic” technologies offer potential tools for identifying PPCPs of potential concern, as well as the most sensitive and vulnerable species.
How can ecotoxicological responses, such as histological and molecular-level responses observed for PPCPs, be translated into traditional ecologically important end points, such as survival, growth, and reproduction of a species? This question is relevant to many other classes of environmental contaminants (Huggett et al. 1992). Responses such as histological changes, behavioral effects, biochemical responses, and up- or down-regulation of genes have been observed in organisms exposed to PPCPs (Ankley et al. 2007; Brooks et al. 2009; Corcoran et al. 2010). These responses are generally not included in current risk assessment schemes but can occur at concentrations that are orders of magnitude lower than concentrations at which effects are observed in regulatory tests, such as acute studies examining effects on fish and invertebrate mortality, or chronic studies looking at effects on reproduction and growth (Figure 2). The importance of these responses in terms of population survival and ecosystem functioning is poorly understood. However, it is necessary to understand these relationships in order to discover the broader implications of nonstandard observations on ecosystem health and to determine the benefits of incorporating data from nonstandard ecotoxicological responses, such as histological and behavioral effects, into prospective and retrospective risk assessment frameworks. Unlike for many other chemical classes, our knowledge of the relationships between effects at the molecular level and effects at the whole-organism level in humans is very well developed. We may therefore be able to apply this knowledge to better understand relationships between molecular, cellular, and whole-organism end points for organisms in the natural environment.
How can ecotoxicity test methods that reflect the different modes of action of active PPCPs be developed and implemented in customized risk assessment strategies? Existing risk assessment approaches for PPCPs in Europe and North America employ standard Organisation for Economic Co-operation and Development (OECD) test methods for examining effects on organisms (CDER 1998; CHMP 2006; CVMP 2000, 2004). Some authorities can ask for nonstandardized studies when a risk cannot be ruled out by standard tests. Concerns have been raised over whether standard methods will identify ecologically important effects of specifically acting PPCPs (Brooks et al. 2009; ECETOC 2008). The effect of the nonsteroidal, anti-inflammatory compound diclofenac on vulture populations (Oaks et al. 2004) is one example of an end point that would not have been predicted from standard studies. Further work is required to understand the effects of PPCPs with different modes of action on aquatic and terrestrial organisms. Depending on the findings of this research, it may be appropriate to develop new guidance on the selection of ecotoxicological test methods (species and end points) in the risk assessment process. However, it would be shortsighted to restrict testing strategies only to methods that reflect specific modes of action because unexpected effects in organisms can occur, as illustrated by the high potency of fluoxetine, a selective serotonin reuptake inhibitor, in algae (Oakes et al. 2010).
How can effects from long-term exposure to low concentrations of PPCP mixtures on nontarget organisms be assessed? Aquatic and terrestrial systems will be exposed to a complex mixture of PPCPs and other contaminants. Many pharmaceuticals, if consumed together at therapeutic doses, can cause severe adverse interactions in humans (e.g., Juurlink et al. 2003). If aquatic organisms respond to these compounds in the same way as humans, effects on the environment could be greater than predicted based on effects data for the single compounds. Antimicrobial PPCPs may also increase persistence of other PPCPs, thus affecting the overall risk (Monteiro and Boxall 2009). Because many human-use PPCPs will be emitted continuously into the environment, organisms in the environment will be exposed throughout their lifetime. However, no regulatory program for prospective environmental risk assessment of PPCPs (or other product classes) takes into account the long-term combined toxicity of mixtures of chemicals, so there is a need to develop new approaches for assessing the risks arising from long-term exposure to mixtures. The concept of mixture risk assessment is gathering momentum, particularly in the public health arena, and recent reports by the European Commission, the UK Committee on Toxicology, and the U.S. National Academy of Sciences have already started to consider this topic (e.g., Kortenkamp et al. 2009). For human medicines, it may be possible to use observed contraindications in humans to provide an indication of whether a particular combination of pharmaceuticals in the environment may be of concern. Mixture interactions could also be simulated by pharmacokinetic modeling, linking models at the interaction site (Krishnan et al. 2002), although this will require extensive quantitative information on pharmacokinetics and/or toxicokinetics. Although the use of in vitro assays for relevant end points (e.g., carcinogenic, mutagenic, and reproductive effects) to assess the effects of mixtures of pharmaceuticals that typically occur in environmental systems may also provide useful information for use in risk assessment, these will need to be extensively validated before use.
Can nonanimal testing methods be developed that will provide equivalent or better hazard data compared with current in vivo methods? For personal care products, there is regulatory pressure in some geographic regions to reduce the amount of animal testing used for human safety and environmental risk assessment in a 3Rs framework (reduce, refine, replace). It may be possible to reduce the amount of animal testing using nonanimal testing methods, such as in vitro approaches and in silico methods (e.g., quantitative structure–activity relationships, read-across and expert systems), by optimizing experimental designs, and by employing intelligent testing strategies (Hutchinson et al. 2003; OECD 2010; Rufli and Springer 2011). Although these approaches are being promoted (e.g., National Academy of Sciences 2007) and used for industrial chemicals [e.g., as part of the REACH (Registration, Evaluation, Authorisation and Restriction of Chemical substances) regulations in Europe and elsewhere (Halder et al. 2010)], additional approaches are needed to replace animal test methods with methods able to evaluate specific and nonspecific modes of action.
Risk and Relative Risks
How can regions where PPCPs pose the greatest risk to environmental and human health, either now or in the future, be identified? Risks of PPCPs in the environment in different geographic regions vary because of differences in the presence/absence and type of manufacturing sites, level of PPCP use, population demographics, cultural practices, environmental and climatic characteristics, dilution potential of receiving environments, and infrastructure related to wastewater and drinking water treatment. Risks may change in the long term due to factors such as increased urbanization and effluent-dominated instream flows (Brooks et al. 2006), increased disease pressures, demographic change, population increases, technological developments (e.g., move from small molecules to biologics, development of nanomedicines, improvements in drug delivery), and climate change. By better understanding the drivers for PPCP exposure in different regions, it may be possible to identify those areas that are at greatest risk, meaning that control options can be focused to areas/regions where they will be most effective. By understanding how risks will change in the longer term, it may be possible to anticipate and preemptively mitigate against unacceptable changes in risks.
How important are PPCPs relative to other chemicals and nonchemical stressors in terms of biological impacts in the natural environment? PPCPs are released into the natural environment along with many other chemicals (e.g., nutrients, metals, industrial chemicals, pesticides, natural hormones). The natural environment is also exposed to nonchemical stressors such as changes in water flow and temperature. The affect of PPCPs could be small compared with the many other chemical and nonchemical stressors present in the natural environment. To make informed management decisions, it is necessary to understand the relative impact of PPCPs compared with other pressures in a particular situation.
Do PPCPs pose a risk to wildlife such as mammals, birds, reptiles, and amphibians? Most studies have focused on effects of PPCPs on fish and invertebrates, but our knowledge of risks to other wildlife species, such as birds and small mammals, is less developed. Several case studies have highlighted the importance of understanding effects on birds and mammals. For example, the inappropriate use of diclofenac and associated cultural practices regarding disposal of animal carcasses, combined with the high sensitivity of vultures to diclofenac, were responsible for the decline in populations of three vulture species in Asia (Oaks et al. 2004), resulting in ecological, socioeconomic, cultural, and human health impacts (Markandya et al. 2008). Indirect effects on top predators may also be important; for example, there is concern that antiparasitic veterinary medicines may be indirectly affecting populations of insect-eating bats and birds by affecting the quantity of food available (McCracken 1993). More work is needed to better understand the exposure of birds, mammals, and amphibians to PPCPs, as well as the potential toxicological effects of PPCPs on these species.
How can the environmental risks of metabolites and environmental transformation products of PPCPs be assessed? Pharmaceuticals may be metabolized in the treated human or animal so that a mixture of parent compound and metabolites will be released into the environment. Transformation of PPCPs will also occur in wastewater treatment processes, surface waters, sediments, manure, soils, and drinking water treatment processes (Escher and Fenner 2011). Although metabolites and transformation products are usually less hazardous than the parent compound, data for pesticides indicate that some can be more toxic (Sinclair and Boxall 2003). The environmental fate of these substances can also be different from the parent compound, meaning that environmental compartments that are not exposed to the parent may be exposed to a transformation product (Boxall et al. 2004). Concerns have also been raised over the potential human health effects of selected transformation products of PPCPs, such as the halogenated and nitrosamine products resulting from transformation in wastewater and drinking water treatment processes (Sedlak and von Gunten 2011). We need to better understand the release and formation of transformation products of PPCPs in the environment and develop approaches for identifying transformation products that could pose a greater risk than the parent compound.
How can data on the occurrence of PPCPs in the environment and quality of ecosystems exposed to PPCPs be used to determine whether current regulatory risk assessment schemes are effective? Environmental risk assessments for PPCPs have been required in Europe and North America for some time. The effectiveness of these prospective risk assessment approaches, in terms of predicting exposure and effects in the real world, is not always clear. By bringing together data on the occurrence of PPCPs in different regions, as well as information on the status of biological communities and ecosystems, it may be possible to establish whether environmental risk assessment schemes really work for PPCPs. This is a general issue relevant to other classes of chemicals that require an environmental risk assessment. The application of ecoepidemiological approaches that link chemical pressures to effects on ecosystems (e.g., De Zwaart et al. 2006) may help answer this question.
Does environmental exposure to PPCP residues result in the selection of antimicrobial-resistant microorganisms, and is this important in terms of human health outcomes? The WHO (1998) identified the emergence of antimicrobial resistance as one of the serious concerns of health policies in the future. One of the major concerns relating to the occurrence of antibiotic compounds in the environment is the potential for selection of resistant microbial species. Antibiotics in the environment may enhance the formation of single, cross-, and multiple-resistance in bacteria (e.g., Byrne-Bailey et al. 2009; Gaze et al. 2011; Knapp et al. 2010; Kristiansson et al. 2011). However, the role of environmental residues of antibiotics in the selection of antibiotic resistance is still unclear; even where information exists, it is only available for a few antibiotics (e.g., sulfonamides, fluoroquinolones). We need to better understand how antibiotic residues in the environment are involved in selecting for antibiotic resistance, as well as the potential for the acquired resistance to transfer to human and animal pathogens and thus affect human health. This assessment must be interpreted against the backdrop of antibiotic resistance (the resistome) naturally found in the environment or caused by inappropriate clinical use of antibiotics or other environmental contaminants.
How can the risks to human health that arise from antibiotic resistance selection by PPCPs in the natural environment be assessed? Current regulatory paradigms do not consider the potential for antibiotic resistance selection in soils and surface waters. If the occurrence of antibiotics in the natural environment is demonstrated to be an important driver for resistance selection, it may be necessary to develop approaches for considering resistance selection in the natural environment as an end point in the safety assessment of new antibiotic substances. There is also a need to understand the extent to which feces from treated animals and humans act as an environmental source of resistant microorganisms and associated genetic elements.
If a PPCP has an adverse environmental risk profile, what can be done to manage and mitigate the risks? In the event that a PPCP poses an unacceptable risk to the environment, options exist for minimizing or removing emissions to the environment, including a) substitution of the compound with a more environmentally benign compound; b) development of better drug delivery systems so that smaller doses are needed; c) improvement of packaging and package sizes to extend shelf life and reduce the amount of the product that expires and must be discarded unused; d) changes in prescription and animal husbandry practices; and e) introduction of improved wastewater treatment options (e.g., Daughton 2003a, 2003b; START 2008). However, the efficacy and practicality of many of these solutions is poorly understood. A systematic study is needed to determine the benefits of different management and mitigation options and any societal and environmental costs associated with a particular option in different regions of the world. This will allow informed decisions to be made on the best mitigation strategy.
What effluent treatment methods are effective in reducing the effects of PPCPs in the environment while not increasing the toxicity of whole effluents? During biological treatment, some PPCPs may be degraded or removed through sorption to sludge (Prasse et al. 2011; Ternes et al. 2004). Recalcitrant PPCPs may be removed using tertiary treatment methods such as ozonation, activated carbon adsorption, or nanofiltration (Ternes et al. 2004). In some cases, the wastewater treatment process may increase the risk. For example, ozonation may result in the formation of more toxic oxidation products. In other cases, the introduction of a treatment option may move the exposure from one environmental compartment to another. For example, introduction of procedures to enhance sorption of PPCPs to activated sludge treatment will mean that while emissions to water bodies are reduced, exposure of the terrestrial environment will increase when the sludge is applied to soils as a fertilizer (McClellan and Halden 2010). Increased knowledge is required to determine the effectiveness and consequences of waste and drinking water treatment options on PPCP fate and effects.
How can the efficacy of risk management approaches be assessed? The introduction of risk management strategies can result in environmental, economic, and societal costs. In these cases, management options should be proven to be effective at reducing environmental impacts before they are widely introduced. Guidance is needed in evaluating environmental monitoring approaches to determine the efficacy of particular management options. These approaches should not only include monitoring of changes in the occurrence of a particular substance but also be able to monitor changes (improvements) in the health of the ecosystem of interest. The costs (economic, social, and environmental) of a management option also need to be considered. Control options for antimicrobial compounds (e.g., banning of antibiotic substances as growth promoters and/or prophylactic treatments in agriculture) may not be effective in controlling antibiotic resistance because once antibiotic resistance genes are present in the environment, they may not disappear. Other anthropogenic compounds will also facilitate the selection of microrganisms that are resistant to some classes of antibiotic (e.g., Gaze et al. 2011).
Ranking of Questions and Next Steps
When questions were ranked in terms of importance, the question regarding the relative risks of PPCPs compared with other environmental stressors was identified as the most important (Table 1). This reflects the significance of the question for allocation of future research resources and the implementation of future policy development and risk management options. If the answer to the question is that PPCPs are more important stressors than are other stressors in the environment, then many other questions identified in this exercise will be relevant and important. However, if PPCPs pose relatively minor risks compared with other stressors in the environment, then expending large amounts of resources answering the other questions may not offer the best use of resources in terms of global environmental protection. Questions regarding prioritization, improved characterization of effects, and antibiotic resistance were also ranked highly, whereas questions regarding risks of nonextractable residues, treatment, and the use of nonanimal studies were ranked lower (Table 1). For each question, potential approaches that could be adopted to address the question were identified. We envisage that this information will be invaluable in formulating future research programs involving the risks of PPCPs in the environment.
In the development of future research and policy initiatives, it is important to recognize that many of the questions are interrelated and that knowledge gained from one question may be needed to address other questions (Table 1). In some instances, it may be necessary to address a lower-ranked question before a high-ranked question can be fully answered. For example, knowledge gained from answering questions around prioritization of PPCPs, the importance of the environment as a selection pressure for antimicrobial resistance, identification of regions of greatest risk, and characterization of risks to wildlife may all need to be answered before the top-ranked question can be addressed. The level of challenge associated with answering a question also varies (Table 1). Questions regarding the risks of nonextractable residues and prioritization of PPCPs may be addressable with limited investment over relatively short time periods compared with other questions.
Many questions (e.g., the questions involving NERs, mixture interactions, and extrapolation of results on molecular and cellular effects to ecologically relevant end points) are not unique to PPCPs, so it may be appropriate to address these in broader research programs looking at other chemical classes. However, the detailed understanding that we have for the effects of many PPCPs on humans might make them good candidate model compounds for addressing some of these wider questions.
Wider Global Relevance of the Exercise
Although participants from different regions of the world were engaged in the exercise, most question submissions (92%) were from North America (46.6%), Europe (29.8%), and Australia/New Zealand (15.5%). The workshop was also dominated by North American (51%) and European attendees (14.6%) and representatives of multinational corporations (34%). Two subsequent regional workshops were held in South Korea and Australia to determine the relevance of the 20 questions to the East Asian and Australia/New Zealand regions, respectively, and to identify additional questions that may be important to these regions. Participants at these workshops agreed that the 20 questions were of high importance to the East Asian and Australasian regions, and they highlighted the fact that these regions had unique characteristics (e.g., in terms of biodiversity) that should be considered when addressing the questions. Participants felt that important issues, such as better risk communication, consideration of cultural differences, and the impacts of natural medicines had also been overlooked. The conclusions of these later workshops will be presented in detail elsewhere.
The present study is the first to use the key question approach to identify key issues regarding exposure, effects, and risks of PPCPs in the environment. We see this exercise as the start of a broader program, and in the short term we are planning a broader global survey to identify which questions are most relevant to different stakeholders and why (additional questions proposed by the “local” workshops will be included in this exercise). In addition to this survey, additional workshops are planned on select topics (e.g., antibiotic resistance), and the conclusions of the survey and the workshops will be disseminated to policy makers around the world. We are optimistic that the results of this exercise will be invaluable in informing the design, coordination, and implementation of future research programs on PPCPs in the environment. We hope that these programs will help us to better understand the potential and relative risks of these substances in the natural environment and to effectively control and manage these risks.
Byrne-Bailey KG, Gaze WH, Kay P, Boxall ABA, Hawkey PM, Wellington EMH. 2009. Prevalence of sulfonamide resistance genes in bacterial isolates from manured agricultural soils and pig slurry in the United Kingdom. Antimicrob Agents Chemother 53:696–702.
Caldwell DJ, Mastrocco F, Hutchinson TH, Länge R, Heijerick D, Janssen C, et al. 2008. Derivation of an aquatic predicted no-effect concentration for the synthetic hormone, 17α-ethinyl estradiol. Environ Sci Technol 42:7046–7054.
Capelton AC, Courage C, Rumsby P, Holmes P, Stutt E, Boxall ABA, et al. 2006. Prioritising veterinary medicines according to their potential indirect human exposure and toxicity profile. Toxicol Lett 163:213–223.
CDER (Center for Drug Evaluation and Research). 1998. Guidance for Industry: Environmental Assessment of Human Drug and Biologics Applications. Washington, DC:CDER and Center for Biologics Evaluation and Research, Food and Drug Administration. Available: http://www.fda.gov/downloads/Drugs/GuidanceComplianceRegulatoryInformation/Guidances/ucm070561.pdf [accessed 17 July 2012].
CHMP (Committee for Medicinal Products for Human Use). 2006. Guideline on the Environmental Risk Assessment of Medicinal Products for Human Use. EMEA/CHMP/SWP/4447/00 corr 1. London:European Medicines Agency. Available: http://www.ema.europa.eu/docs/en_GB/document_library/Scientific_guideline/2009/10/WC500003978.pdf [accessed 17 July 2012].
CVMP (Committee for Medicinal Products for Veterinary Use). 2000. VICH Topic GL6 (Ecotoxicity Phase I) Step 7: Guideline on Environmental Impact Assessment (EIAs) for Veterinary Medicinal Products–Phase I. CVMP/VICH/592/98. London:European Agency for the Evaluation of Medicinal Products. Available: http://www.ema.europa.eu/docs/en_GB/document_library/Scientific_guideline/2009/10/WC500004394.pdf [accessed 17 July 2012].
CVMP (Committee for Medicinal Products for Veterinary Use). 2004. Guideline on Environmental Impact Assessment for Veterinary Medicinal Products Phase II. CVMP/VICH/790/03-FINAL. London:European Agency for the Evaluation of Medicinal Products. Available: http://www.ema.europa.eu/docs/en_GB/document_library/Scientific_guideline/2009/10/WC500004393.pdf [accessed 17 July 2012].
CVMP (Committee for Medicinal Products for Veterinary Use). 2008. Revised Guideline on Environmental Impact Assessment for Veterinary Medicinal Products in Support of the VICH Guidelines GL6 and GL 38. EMEA/CVMP/ERA/418282/2005-Rev.1. London:European Agency for the Evaluation of Medicinal Products.
Daughton CG. 2003a. Cradle-to-cradle stewardship of drugs for minimizing their environmental disposition while promoting human health. I. Rationale for and avenues toward a green pharmacy. Environ Health Perspect 111:757–774.
Daughton CG. 2003b. Cradle-to-cradle stewardship of drugs for minimizing their environmental disposition while promoting human health. II. Drug disposal, waste reduction, and future directions. Environ Health Perspect 111:775–785.
ECETOC (European Centre for Ecotoxicology and Toxicology of Chemicals). 2008. Intelligent Testing Strategies in Ecotoxicology: Mode of Action Approach for Specifically Acting Chemicals. TR 102, Brussels:ECETOC.
FASS.se. 2012. FASS.se För Allmänheten. Available: http://www.fass.se/LIF/home/index.jsp [accessed 24 July 2012].
Gaze WH, Zhang L, Abdouslam NA, Hawkey PM, Calvo-Bado L, Royle J, et al. 2011. Impacts of anthropogenic activity on the ecology of class 1 integrons and integron-associated genes in the environment. ISME J 5:1253–1261.
Gunnarsson L, Jauhiainen A, Kristiansson E, Nerman O, Larsson DGJ. 2008. Evolutionary conservation of human drug targets in organisms used for environmental risk assessments. Environ Sci Technol 42:5807–5813.
Huggett DB, Cook JC, Ericson JF, Williams RT. 2003. A theoretical model for utilizing mammalian pharmacology and safety data to prioritize potential impacts of human pharmaceuticals to fish. Hum Ecol Risk Assess 9:1789–1799.
Hutchinson TH, Barrett S, Buzby M, Constable D, Hartmann A, Hayes E, et al. 2003. A strategy to reduce the numbers of fish used in acute toxicity testing of pharmaceuticals. Environ Toxicol Chem 22:3031–3036.
Kim J-W, Ishibashi H, Yamauchi R, Nobohiro I, Takao Y, Hirano M, et al. 2009. Acute toxicity of pharmaceutical and personal care products on freshwater crustacean (Thamnocephalus platyurus) and fish (Oryzias latipes). J Toxicol Sci 34:227–232.
KNAPPE (Knowledge and Need Assessment of Pharmaceutical Products in Environmental Waters). 2008. Knowledge and Need Assessment of Pharmaceutical Products in Environmental Waters: Final Report. Available: http://cordis.europa.eu/documents/documentlibrary/124584761EN6.pdf [accessed 17 July 2012].
Kolpin DW, Furlong ET, Meyer MT, Thurman EM, Zaugg SD, Barber LB, et al. 2002. Pharmaceuticals, hormones, and other organic wastewater contaminants in U.S. streams, 1999–2000: a national reconnaissance. Environ Sci Technol 36:1202–1211.
Krishnan K, Haddad S, Béliveau M, Tardif R. 2002. Physiological modeling and extrapolation of pharmacokinetic interactions from binary to more complex chemical mixtures. Environ Health Perspect 110(suppl 6):989–994.
Kristiansson K, Fick J, Janzon A, Grabic R, Rutgersson C, Weidegård B, et al. 2011. Pyrosequencing of antibiotic-contaminated river sediments reveals high levels of resistance and gene transfer elements. PLoS ONE 6:e17038; doi:10.1371/journal.pone.0017038 [Online 6 February 2011].
Markandya A, Taylor T, Longo A, Murty MN, Murty S, Dhavala K. 2008. Counting the cost of vulture decline—an appraisal of the human health and other benefits of vultures in India. Ecol Econ 67:194–204.
Oakes KD, Coors A, Escher BI, Fenner K, Garric J, Gust TM, et al. 2010. Environmental risk assessment for the serotonin re-uptake inhibitor fluoxetine: case study utilizing the European risk assessment framework. Integr Environ Assess Manag 6(suppl 1):524–539.
OECD (Organisation for Economic Co-operation and Development). 2010. Short Guidance on the Threshold Approach for Acute Fish Toxicity. Series on Testing and Assessment no. 126. ENV/JM/MONO(2010)17. Paris:OECD. Available: http://iccvam.niehs.nih.gov/SuppDocs/FedDocs/OECD/OECD-GD126.pdf [accessed 18 July 2012].
Ramirez AJ, Brain RA, Usenko S, Mottaleb MA, O’Donnell JG, Stahl LL, et al. 2009. Occurrence of pharmaceuticals and personal care products (PPCPs) in fish tissues: results of a national pilot study in the United States. Environ Toxicol Chem 28:2587–2597.
Rudd MA, Beazley K, Cooke SJ, Fleishman E, Lane DE, Mascia MB, et al. 2011. Generation of priority research questions to inform conservation policy and management at a national level. Conserv Biol 25:476–484.
START. 2008. Pharmaceuticals for Human Use: Options of Action for Reducing the Contamination of Water Bodies. Frankfurt, Germany:Institute for Social-Ecological Research. Available: http://www.start-project.de/downloads/start_Practical_Guide.pdf [accessed 17 July 2012].
Trudeau VL, Metcalfe CD, Mimeault C, Moon TW. 2005. Pharmaceuticals in the environment: drugged fish? In: Environmental Toxicology; Biochemistry and Molecular Biology of Fishes (Mommsen TP, Moon TW, eds), Vol 6. Amsterdam:Elsevier, 475–493.
WHO (World Health Organization). 1998. Antimicrobial Resistance. Fact Sheet no. 194. Geneva:WHO. Available: http://www.who.int/mediacentre/factsheets/fs194/en/ [accessed 18 July 2012].
WHO (World Health Organization). 2011. Pharmaceuticals in Drinking Water. WHO/HSE/WSH/11.05. Geneva:WHO. Available: http://www.who.int/water_sanitation_health/publications/2011/pharmaceuticals_20110601.pdf [accessed 18 July 2012].
We are pleased to announce our new impact factor of 9.78, up from 8.44 last year. Based on our impact factor, EHP is now #4 out of 229 Environmental Science journals, #4 out of 176 Public, Environmental & Occupational Health journals, and #2 out of 92 Toxicology journals. Thanks to all the authors, reviewers, readers, and EHP staff who have contributed to our success.
EHP is pleased to announce that it is now operating under a continuous publication workflow! As indicated in a previous announcement, continuous publication allows EHP to post new content online throughout the month, as each paper becomes ready for an issue. This gets content out to our readers much more quickly than the old issue-based model, and unlike our previous Advance Publication model, these are final, edited articles. (more…)