Frederic D. L.
Leusch
*a and
Shane A.
Snyder
bc
aSmart Water Research Centre, Australian Rivers Institute, School of Environment, Griffith University, Southport Qld 4222, Australia. E-mail: f.leusch@griffith.edu.au
bUniversity of Arizona, 1133 E. James E. Rogers Way, Harshbarger 108, Tucson, AZ 85721-0011, USA
cNational University of Singapore, NUS Environmental Research Institute (NERI), 5A Engineering Drive 1, T-Lab Building, #02-01, Singapore 117411
First published on 10th July 2015
In vitro bioassays, more recently referred to as “bioanalytical tools” in an attempt to emphasize their analytical purpose rather than the uncertain relation to adverse health outcomes, are often thought of as novel tools by water stakeholders. They have, however, been used for over half a century in assessment of recycled water quality. Today, millions of chemicals and formulations are available for commercial use and most have a high propensity to enter sewage collection systems. However, traditional health risk assessment methods involving animal testing at high doses and extrapolation to environmental relevant levels are vastly overwhelmed in capacity by the innumerable chemicals and transformation products potentially present in waters. Beyond the sheer number of chemicals, the interactions of these chemicals as complex mixtures is largely unaddressed in traditional regulatory schemes. Moreover, non-human animal models are often misleading due to differences in metabolism and associated pharmacokinetics. Thus, water professionals continue to struggle with ever increasing numbers of chemicals detected at trace levels in water and the potential interactions of these chemicals during mixture exposures. Bioanalytical tools offer a path forward towards more comprehensive chemical evaluations of water, which can provide greater public confidence in the ability of potable reuse schemes to produce clean and safe drinking water.
Water impactGrowing urban populations and uncertain climatic conditions have in the past decades led to increasingly severe and widespread water shortages, which require integration of novel water sources, such as water reclaimed from wastewater. Alternative water sources can present new chemical challenges that conventional chemical analysis cannot overcome. Bioanalytical tools offer a path forward towards more comprehensive chemical evaluations of water, by detecting chemicals not by their structure but by their biological activity. This provides an improved capacity to detect non-target compounds and some measure of mixture interactions. This is important, as it can provide greater public confidence in the ability of potable reuse schemes to produce clean and safe drinking water. |
Municipal wastewater can contain a wide range of natural and synthetic chemicals, including personal care products, household chemicals, industrial products, natural and synthetic hormones and pharmaceuticals, and chemicals formed during wastewater treatment.4 Some health authorities have therefore produced guidance documents specifically for water intentionally sourced from wastewater, which consider the much larger universe of chemical contaminants potentially present.5,6 Many water recycling schemes have conducted extensive chemical monitoring studies on reclaimed water,7,8 and these rich datasets can be used to determine the likelihood and significance of exceedance of chemical guidelines.9,10 However, even extensive chemical monitoring can only detect a limited subset of the vast number of chemicals that are likely present and only those above a methodologically defined detection limit that is constantly evolving. There are, for example, more than 4000 pharmaceutical compounds,11 up to 70000 compounds in daily use,12 and up to 65
000
000 chemicals and formulations commercially available.13 Beyond the large number of chemicals produced, each one has the propensity to form transformation products both during treatment and in the environment.14 Not only would it be impossible to write a drinking water guideline document that would consider all of those compounds, it is also not feasible to detect each of them by conventional chemical analysis. This is where toxicity testing may be a crucial additional tool to ensure the chemical safety of recycled water.15
Toxicity testing involves collecting whole water samples and testing for a range of toxicological endpoints in biological systems. Toxicity testing with whole animals has been the cornerstone of toxicology for a long time, but ethical and financial drivers to reduce, refine and replace whole animal tests16 combined with recent advances in molecular toxicology17–20 have led to an intense interest in alternative techniques such as in vitro bioassays. In vitro toxicity tests are performed at the molecular or cellular level, usually using concentrated organic extracts from water.21 They can detect the triggering molecular or cellular toxic event that occurs at low environmentally relevant concentrations, often below detection limits of chemical analysis and whole animal toxicity testing.22 The main limitation of in vitro assays is that they lack some of the metabolism and transport (toxicokinetic) mechanisms that modulate toxicity in whole organisms. While in vitro bioassays were developed for screening purposes and there is still much debate about their ability to predict whole-organism effects,15 the gap in our understanding of the link between an in vitro response and an adverse outcome in whole organisms is getting narrower. The concept of Adverse Outcome Pathway (AOP)23 provides a solid framework to link a molecular or cellular event (as measured in vitro) to a whole organism effect,20 providing a promising basis for the future of toxicity testing.24–26
In an attempt to emphasize their analytical purpose rather than the uncertain relation to adverse health outcomes, in vitro bioassays applied to water quality testing are sometimes referred to as “bioanalytical tools”.21 Bioanalytical tools are well-suited to monitoring of water quality, as they are significantly faster and cheaper than whole animal toxicity testing, are amenable to high-throughput screening, and allow the generation of relatively rapid toxicology data without the need for ethically and financially expensive whole-animal experimentation.16 In recent years, there has been a move towards standardising the various in vitro techniques available, with the creation of the European Centre for the Validation of Alternative Methods (ECVAM) in 1991 and the US National Toxicology Program Interagency Centre for the Evaluation of Alternative Toxicological Methods (NICEATM) in 1998. These two programs, and similar efforts by Organisation for Economic Cooperation and Development (OECD), have published an ever-growing catalogue of defined operating protocols for the testing of chemicals.
Bioanalytical tools are increasingly applied to water quality assessment21,27 and, considering the predicaments of conventional chemical risk assessment with complex water sources such as treated sewage, it is only logical to apply bioanalytical techniques in the context of recycled water quality assessment. A few bioanalytical tools have in fact been applied since the 1960s to assessment of recycled water quality, but recent developments have greatly expanded the number and scope of in vitro tools available for (recycled) water quality testing.
In the context of potable reuse, applying a gastro-intestinal or liver human cell model would appear to be the most suitable. The bacterial assays are clearly more sensitive than the mammalian cytotoxicity assays,28 although it is more difficult to relate bacteria toxicity results to potential human health risks. On the other hand some of the human cell-based assays have been shown to correlate well with acute animal toxicity tests.35
Toxicity to proteins has not received much attention in water quality assessment, but a recent study suggests a genetically modified bacteria assay (E. coli GSH±) may be suitable with highly treated waters.38
A wide variety of yeast and mammalian reporter gene assays (such as CALUX, GeneBLAzer, yeast estrogen and androgen screen) and cell proliferation assays (such as the E-SCREEN, A-SCREEN and T-SCREEN) have been applied to detect endocrine active compounds in water quality monitoring.39–43
The Imaging-PAM (I-PAM) assay has been widely applied to detect inhibition of photosynthesis in water samples44 and is not surprisingly highly sensitive to herbicides.45
Enzymatic activity, such as interference with the enzyme acetylcholinesterase (AChE), is generally measured with “naked” enzymes (i.e., not in cell-based assay), and can therefore be more sensitive to matrix interference in complex water samples.46 AChE inhibition has nevertheless been tested and detected in water samples, and is commonly associated with potent insecticides.32,36
Scheme/site name | Endpoints (assays) | Reference(s) |
---|---|---|
a Please refer to original citation for assay name abbreviations. Other abbreviations used here: “LDH” = Lactate Dehydrogenase; “AChE” = Acetylcholinesterase. | ||
Dan Region Sewage Reclamation Project, Israel (1960-present) | Mutagenicity (Ames test) | 55 |
Montebello Forebay Groundwater Recharge Project, California, USA (1962-present) | Mutagenicity (Ames test) | Reviewed in 15 |
Carcinogenicity (mammalian cell transformation assay) | ||
Orange County Water Factory 21 (1975–2004) and Groundwater Replenishment System (2004-present), California, USA | Mutagenicity (Ames test) | 15, 56 |
Potomac Estuary Experimental Water Treatment Plant, Virgina, USA (1980–1982) | Mutagenicity (Ames test) | 15, 57 |
Carcinogenicity (mammalian cell transformation assay) | ||
Tampa Water Resource Recovery Project, Florida, USA (1987–1989) | Mutagenicity (Ames test) | Reviewed in 15 |
Genotoxicity (sister chromatid exchange test) | ||
San Diego Total Resources Recovery Project, California, USA (1981–1999) | Mutagenicity (Ames test) | 15, 61 |
Genotoxicity (micronucleus test, 6-thioguanine resistance assay) | ||
Carcinogenicity (mammalian cell transformation assay) | ||
Tucson Reclaimed Water System, Arizona, USA (1989-present) | Mutagenicity (Ames test) | 102 |
Windhoek Direct Potable Reuse Scheme, Namibia (1968-present), | Cytotoxicity to bacteria (bacterial growth test) | 33, 59, 60 |
Cytotoxicity to human cells (LDH leakage assay with whole blood cells) | ||
Mutagenicity (Ames test) | ||
Neurotoxicity (AChE inhibition) | ||
Immunotoxicity (cytokine production with whole blood cells) | ||
Landsborough Water Reclamation Plant, Queensland, Australia | Cytotoxicity to bacteria (Microtox) | 66, 67 |
Estrogenicity (E-SCREEN, ERBA) | ||
Five water reclamation plants in the USA | Estrogenicity (E-SCREEN, YES) | 68 |
Androgenicity (A-SCREEN, YAS) | ||
Perth Groundwater Replenishment Scheme, Western Australia, Australia (2009-present) | Cytotoxicity to bacteria (Microtox) | 70 |
Genotoxicity (umuC) | ||
Estrogenicity (E-SCREEN) | ||
Androgenicity (AR-CALUX) | ||
Phytotoxicity (I-PAM) | ||
Qld Western Corridor Recycled Water Scheme, Queensland, Australia (2009-present) | Cytotoxicity to bacteria (Microtox) | 36, 72 |
Genotoxicity (umuC) | ||
AhR induction (AhR-CAFLUX) | ||
Estrogenicity (E-SCREEN) | ||
Phytotoxicity (I-PAM) | ||
Neurotoxicity (AChE inhibition) | ||
South Caboolture Water Reclamation Plant, Queensland, Australia | Cytotoxicity to bacteria (Microtox) | 48, 67, 74, 75 |
Estrogenicity (E-SCREEN) | ||
AhR induction (AhR-CAFLUX) | ||
Neurotoxicity (AChE inhibition) | ||
Phytotoxicity (I-PAM) | ||
Genotoxicity (umuC) | ||
Gerringong Water Reclamation Plant, Victoria, Australia | Cytotoxicity to bacteria (Microtox) | 67 |
Estrogenicity (E-SCREEN) | ||
Unidentified water reclamation plant in Queensland, Australia | Cytotoxicity to bacteria (ToxScreen3) | 30 |
Androgenicity (AR-CALUX) | ||
Estrogenicity (ER-CALUX) | ||
Genotoxicity (umuC) | ||
Nine water reclamation plants in various Australian states | Cytotoxicity to human cells (Caco2 NRU, WIL2NS TOX, HepaTOX) | 32 |
Mutagenicity (Ames test) | ||
Genotoxicity (WIL2NS FCMN) | ||
Endocrine activity (CALUX [ERα, AR, GR, PR and TRβ]) | ||
Neurotoxicity (AChE inhibition) | ||
Immunotoxicity (cytokine production with THP1 cells) | ||
MFO induction (HepCYP1A2) | ||
Two water reclamation plants in Australia | Cytotoxicity (AREc32 cell viability, Caco2 NRU, RTG2 MTT, DART lethality, SK-N-SH cytotoxicity, algae growth inhibition, Microtox, Photobacterium phosphoreum T3) | 28 |
Phytotoxicity (I-PAM) | ||
Endocrine activity (CALUX [ERα, AR, GR, PR and TRβ], GeneBLAzer [ER, AR, GR and PR], yeast screen [estrogen and androgen], E-SCREEN, hER yeast, medER yeast, HELN [ERα, ERβ, AR and TR], FACTORIAL [ERE-cis, ERα-trans, AR-trans, GR-trans, THRα1-trans and RORβ-trans], hERα-HeLa-9903, MCF7 [ERE and ARE], steroidogenesis, DART CYP19A1B aromatase, MDA-kb2 [AR and GR], switchgear-GR, T-SCREEN, P19/A15, hRAR yeast assay) | ||
Neurotoxicity (AChE inhibition) | ||
Immunotoxicity (THP1 cytokine production assay) | ||
Mutagenicity (Ames [TA98, TA100 and TAmix]) | ||
Genotoxicity (umuC, micronucleus assay) | ||
Protein toxicity (E. coli GSH±) | ||
Adaptive stress response (FACTORIAL [HSE-cis, HIF-1a-cis, NFκB-cis, Nrf2/ARE-cis and p53-cis], DART HSPB11 induction, switchgear-hypoxia, GeneBLAzer [NFκB and p53], CALUX [NFκB, Nrf2 and p53], Jurkat E6.1 IκB, AREc32, Nrf2-keap) | ||
Xenobiotic metabolism (FACTORIAL [PXR-cis, PXR-trans, CAR-trans, PPARγ-cis, PPARγ-trans and AhR-cis], HG5LN PXR, CAR-yeast, CALUX [PPARα and PPARγ], MCF7-PPAR, PPARγ-GeneBLAzer, AhR-yeast, AhR-CAFLUX, H4IIEluc, MCF7-DRE, DART CYP1A induction) |
A 1978 study applied the Ames assay to test the effect of ozonation on the mutagenicity of reclaimed water for groundwater recharge in Israel.55 The Dan Region Sewage Reclamation Project is a groundwater recharge scheme established in the 1960s that receives treated wastewater from eight wastewater treatment plants in Tel Aviv. After a basic mechanical and biological treatment step, the water is injected into the local aquifer and used mostly for agricultural purposes. The study showed no significant difference in mutagenicity between groundwater (reclaimed from wastewater) and distilled water, but ozonation of groundwater led to a 3–6× increase in mutagenicity. However, the specific mutagens could not be identified.
In the USA, the Ames test was applied in the late 1970s and early 80s to water samples collected from various treatment stages at Water Factory 21,56 a managed aquifer project in Orange County, CA (now the Groundwater Replenishment System). The results showed significant mutagenicity in the influent (i.e., treated wastewater) but a significant decrease (to non-detectable) after GAC treatment. Mutagenicity was, however, detected again after subsequent chlorination. Fractionation experiments suggested that the mutagenic activity was associated mostly with hydrophobic organic compounds, but the exact compounds responsible could not be identified.
The Ames test for mutagenicity was combined in the mid-1980s with a mammalian cell transformation assay (which provides a more comprehensive measure of carcinogenic potential but is more cumbersome and time-consuming to perform) to test recycled water produced in both the Montebello Forebay Groundwater Recharge Project and the Potomac Estuary Experimental Water Treatment Plant. The Montebello Forebay scheme is a managed aquifer recharge project in California, USA, in operation since 1962. The Potomac Estuary Experimental Water Treatment Plant was a US Army Corps of Engineers pilot project to provide highly treated water by blending Potomac estuary water with secondary effluent from a municipal WWTP in Washington DC treated by filtration, carbon adsorption and disinfection. In both studies, low-level mutagenic activity was detected in the Ames test with reclaimed water after chlorination, although interestingly the activity was lower than that in other water samples tested for comparison, including groundwater and local drinking water.15,57 More than half of the mutagenic activity in the reclaimed water samples appeared to be due to the chlorination process.15 The cell transformation assay also showed a small number of positive samples with both the reclaimed water and the local drinking water.57 The study concluded that the reclaimed water did not indicate any increase in potential chronic health effects compared to local drinking water, although a subsequent review commented that the limited number of toxicity tests was insufficient to clearly establish the safety of the water.15
Similar results were obtained in a study at the Stander Reclamation Plant in Pretoria, South Africa, a plant producing 4.5 ML d−1 of reclaimed water by coagulation, sand filtration, activated carbon absorption and chlorination. Carcinogenic activity, determined by cell transformation assay, was lower in reclaimed water than in local tap water.58
In the late 1980s, a study on a pilot plant in Florida also applied the Ames test for mutagenicity, but this time combining it with a sister chromatid exchange assay for genotoxicity (reviewed in ref. 15). The Water Resource Recovery Project in Tampa was a pilot plant to evaluate the acceptability of using reclaimed water to augment the city's water supply. The final treatment train included GAC and disinfection with ozone. No mutagenic or genotoxic activity was observed in any of the samples. This project provides an interesting early insight into some of the power of quick and rapid in vitro bioassay use during the early design stage. Three different treatment trains were initially trialled (GAC, RO and UF), but the project proponents settled on GAC based on better results with the Ames test. Likewise, ozonation was selected as disinfection agent instead of chlorine because the latter produced mutagenic activity in the final water. Extensive toxicity testing during validation, including chronic toxicity tests in whole animals, confirmed that the selected treatment train had no adverse effect on any of the endpoints monitored.15
Regular bioassay testing has also been carried out at the direct potable reuse plant in Windhoek, Namibia. The Goreangab Water Reclamation Plant has had several upgrades since the start of operations in 1968, with the current advanced water treatment train producing 21 ML d−1 with a treatment train consisting of high dose ozonation, activated carbon, and ultrafiltration (O3/BAC + GAC/UF) followed by chlorination. The monthly testing regime includes in vitro assays such as the Ames test and a bacterial growth inhibition assay.59 The source water (treated sewage) was on occasion mutagenic (up to 2.9× increase in number of revertants), however the reclaimed water never induced significant mutagenicity (all results <2× increase).60 Inhibition of bacterial growth was evident with both the source and product waters, with up to 34% inhibition of bacterial growth in reclaimed water. The authors attribute this inhibition to occasionally high iron, aluminium and manganese concentrations.60
Extending the bioassay battery yet further (but still focussing only on reactive toxicity), Olivieri et al.61 applied the Ames test for mutagenicity, the micronucleus test for genotoxicity, the 6-thioguanine resistance assay for mutagenicity in mammalian cells and mammalian cell transformation assay for carcinogenicity to reclaimed water from the Total Resources Recovery Project in San Diego, a pilot plant that included UV, RO and GAC to reclaim water for indirect potable reuse (reviewed in ref. 15). The results show weak mutagenic activity in both reclaimed and drinking water source waters, with lower activity in reclaimed water compared to the conventional alternative. The results with the mammalian cell transformation assay were not repeatable and were thus rejected, and the remaining two assays did not show any mutagenic or genotoxic activity in either water samples.15 The study, which also included additional chemical and microbiological tests, concluded that the health risks associated with the use of reclaimed water as a raw water supply were less or equal to the raw water sources used then.61
Several studies in the late 1980s and early 90s tried to identify mutagenic and genotoxic compounds in water (mostly drinking water, reviewed in ref. 62–64). Those studies confirmed that chlorination by-products were likely the cause of the reactive toxicity in water. Several highly mutagenic compounds were identified, such as MX,15 but even those compounds could not account for the total reactive toxicity in water samples, and the identity of the causative compound(s) is still unclear to this day. The results clearly emphasized that exposure to chlorination disinfection by-products in water should be minimized, although proper pathogen control should never be compromised.
A 2005 study measured estrogenic activity at the Landsborough Water Reclamation Plant in Australia66 using two bioassays: an estrogen receptor binding assay (ERBA) and the E-SCREEN. The treatment train consists of ozonation, biological activated carbon and UV treatment (O3/BAC/UV). Both assays detected high estrogenic activity in sewage influent, but the treatment train was very effective and no activity was detected in the final effluent: <0.75 ng L−1 and <0.03 ng L−1 EEQ in the ERBA and E-SCREEN, respectively. The same plant was investigated again in 2010 using the Microtox and the E-SCREEN assays.67 Low activity was detected in both bioassays, up to 0.94 mg L−1 Toxic Equivalents (TEQ) in the Microtox (51–60% lower than secondary treated wastewater) and up to 0.07 ng L−1 EEQ in the E-SCREEN (94–96% lower).
A 2006 study applied four bioassays for estrogenic and androgenic endocrine activity (E-SCREEN, A-SCREEN, yeast estrogen and yeast androgen screen) to test water from five unspecified water reclamation facilities in several US states.68 The results show that estrogenic and androgenic activity were detected in treated sewage (0.2–7.9 ng L−1 EEQ in the E-SCREEN and 1.6–9.1 ng L−1 testosterone equivalents, TTEQ, in the A-SCREEN), but that soil aquifer treatment and reverse osmosis were very effective at reducing the residual endocrine activity to below detection limits (<0.04 ng L−1 EEQ and <1 ng L−1 TTEQ). The results of the estrogenic bioassays were well correlated with chemical analysis of estrogen hormones, but androgenic activity was higher than predicted, indicating the likely presence of unknown androgenic compounds.
Two large scale projects in particular deployed batteries of bioanalytical tools to examine water quality: the Perth Groundwater Replenishment Scheme (GWRS) and the Queensland Western Corridor Recycled Water Scheme (WCRWS). The GWRS is a 75 ML d−1 scheme to reclaim water from urban wastewater by microfiltration and reverse osmosis (MF/RO) for aquifer recharge in Perth, Western Australia. A one-year study in 2008/09 combined chemical analysis with 5 in vitro bioassays (Microtox, umuC, I-PAM, E-SCREEN and AR-CALUX).70,71 The MF/RO treatment significantly reduced biological response in all assays, and only minimal basal toxicity was detected in the final effluent: up to 0.41 toxic units (TU) in the Microtox (56–>82% lower than secondary treated sewage), <0.04 genotoxic units (GTU) in the umuC+S9 and −S9, <0.03 μg L−1 diuron equivalents (DEQ) in the I-PAM, <1 ng L−1 EEQ in the E-SCREEN and <2.5 ng L−1 dihydrotestosterone equivalents (DHTEQ) in the AR-CALUX. Overall, the bioanalytical results confirmed the chemical results and showed MF/RO treatment was very effective at removing biologically active chemicals, with the reclaimed water of comparable quality to ultrapure laboratory grade water.70,71 These findings were again confirmed by a 2014 study at the same site, which showed a reduction in the bioassay response of 92% in the Microtox assay, 89% in the AREc32 oxidative stress assay, and >90% in both the I-PAM and umuC−S9 assays after treatment.51 The latter study combined bioassay analysis with comprehensive chemical analysis of almost 300 chemicals and showed that while both chemical and bioassay analysis showed the same extensive chemical removal by MF/RO, even the thorough screening of 300 chemicals could only account for 1–3% of the non-specific and reactive bioassay responses. This suggests that chemical and bioassay analysis methods only overlap to a small extent and that they are clearly complementary.
The WCRWS was designed to reclaim water from combined urban wastewater in Southeast Queensland by microfiltration, reverse osmosis and advanced oxidation (MF/RO/AO) and supplement a local drinking water dam, producing up to 250 ML d−1 (although it is currently not in operation due to wet climatic conditions). A variety of in vitro bioassays were applied to water produced from the WCRWS, including Microtox, AChE inhibition, I-PAM, E-SCREEN, AhR-CAFLUX, and umuC bioassays.36,72 Again, final effluent samples showed very low activity in all bioassays: up to 0.12 mg L−1 TEQ in the Microtox (87% decrease from secondary treated effluent), <0.06 μg L−1 parathion equivalent (PTEQ) in the AChE inhibition assay, up to 0.05 μg L−1 DEQ in the I-PAM (81% decrease), <0.01 ng L−1 EEQ in the E-SCREEN, up to 0.08 ng L−1 TCDDEQ in the AhR-CAFLUX (93% decrease), <0.05 μg L−1 4NQOEQ in the umuC−S9 and <0.8 μg L−1 BaPEQ in the umuC+S9. Interestingly, the same study also applied the same assays to a variety of other water samples from the urban water cycle, including surface, wastewater, drinking water and ultrapure laboratory blanks. The water produced by the WCRWS was better than current drinking water in all bioassay results, and almost identical to the ultrapure laboratory blank.36,72
A study funded by the National Water Commission of Australia investigated seven unidentified membrane water reclamation plants (5 RO and 2 UF) in several Australian states.32,73 A broad battery of 13 in vitro bioassays was applied: three assays for human cell cytotoxicity (Caco2-NRU, WIL2NS TOX and HepaTOX), two reactive toxicity assays (Ames and WIL2NS FCMN), six assays for specific toxicity (ERα-CALUX, AR-CALUX, GR-CALUX, PR-CALUX, TRβ-CALUX and acetylcholinesterase inhibition assay), one adaptive stress response (CPA in THP1 human monocyte cells) and one xenobiotic metabolism assay (HepCYP1A2). Biological activity was detectable in 10 out of 13 assays in the secondary treated effluent, and while UF/UV treatment had only minimal (if any) effect on the measured activity at the two UF plants, only 3 bioassays produced a response in the RO effluent: up to 0.87 ng L−1 EEQ and 4.4 μg L−1 Tamoxifen Equivalents (TMXEQ) in the ER-CALUX assay (66–>99% decrease from secondary treated sewage), up to 0.61 μg L−1 Dexamethasone Equivalents (DexaEQ) in the THP1-CPA (15–>98% decrease), and up to 0.09 TU in the WIL2NS TOX assay. The biological response in the final RO effluent was tentatively attributed to plasticizers from the RO membranes and disinfection by-products.32,73
Several studies between 2009 and 2012 have combined chemical analysis and a mix of bioassay methods including non-specific (Microtox, ToxScreen3), specific (E-SCREEN, ER-CALUX, AR-CALUX, AhR-CAFLUX, AChE inhibition, I-PAM) and reactive (umuC) toxicity assays to smaller non-RO water reclamation plants, including the South Caboolture Water Reclamation Plant (O3/BAC/O3),48,67,74,75 an unidentified Water Reclamation Plant for non-potable reuse in Queensland (MF/UF/UV),30 and the Gerringong Water Reclamation Plant (O3/BAC/MF/UV).67
Overall, these studies showed that alternative (non-RO) treatments can also be very effective at reducing the biological response, but the final effluent of the advanced water treatment plant often had detectable (albeit very low) activity in many of the assays: 0.57–0.72 mg L−1 TEQ in the Microtox (67–84% decrease from secondary treated effluent), <0.13 ng L−1 EEQ in the E-SCREEN and ER-CALUX (>99% decrease), up to 0.36 ng L−1 TCDDEQ in the AhR-CAFLUX (46–69% decrease), <0.01–0.04 GTUECIR1.5 in the umuC−S9 (83–>92% decrease), up to 0.03 GTUECIR1.5 in the umuC+S9, up to 1.2 μg L−1 PTEQ in the AChE inhibition (57–>90% decrease), and up to 0.05 μg L−1 DEQ in the I-PAM assay (50–>91% decrease). These results were comparable to those obtained using a mix of in vitro bioassays (including Microtox, algae inhibition assays, YES, YAS, I-PAM, AChE inhibition, AhR induction in the yeast dioxin screen, and the umuC assay) to investigate the efficacy of ozonation to reduce biological activity in Swiss and German wastewater treatment plant effluents.76,77
The increase in scope of bioanalytical batteries have of course been mirrored worldwide. At the Goreangab Water Reclamation Plant for example, four in vitro assays have recently been applied to test water quality, including an AChE inhibition assay (neurotoxicity), an LDH leakage assay with whole blood cells (cytotoxicity), and two cytokine production assays (IL-6 and IL-10) in whole blood cultures (immunotoxicity).33 The results show a reduction of biological response in the final effluent compared with the secondary treated sewage influent, up to 6% activity in the AChE inhibition assay (72–>95% decrease from secondary treated sewage), <1% cytotoxicity in the LDH leakage assay (>96% decrease), up to approximately 110 pg mL−1 IL6 in the first CPA (84–>99% decrease), and <1 pg mL−1 IL-10 in the second CPA (>99% decrease).
To evaluate the suitability of this ever expanding catalogue of bioanalytical tools to benchmark water quality and to assess efficacy of water treatment processes, a recent inter-laboratory study28 screened water samples from two Australian water reclamation plants (one RO/AO, the other ozonation and BAC) with a battery 103 different in vitro bioassays: 10 assays for cytoxicity (including Microtox and Caco2-NRU), 46 for specific toxicity (including the I-PAM and various assays for endocrine activity), 12 for reactive toxicity (including Ames and umuC tests), 16 for adaptive stress response and 19 for xenobiotic metabolism (including the AhR-CAFLUX). The study found that source water (treated sewage) produced a biological response in 53 and 60 out of 103 bioassays at each plant, but that advanced water treatment reduced the biological response in all bioassays, to below detection limit in most. The reclaimed water produced a low but detectable response in 5 and 13 of the 103 bioassays for the RO/AO and O3/BAC plants, respectively. The five assays responsive with RO/AO reclaimed water were two bacterial toxicity assays (Microtox and another bioluminescent bacteria assay), the Ames test, and two assays that detect induction of xenobiotic metabolism (specifically the AhR and CAR pathways). The reclaimed water from the O3/BAC plant produced a detectable response in those same assays as well as another Ames tests, the ER-CALUX assay, two assays for oxidative stress (a type of adaptive stress response) and four additional xenobiotic metabolism assays (for the AhR, CAR and PXR pathways). Overall, the study suggests that early indicators of cellular responses (adaptive stress response and xenobiotic metabolism), which are not measures of toxicity per se, may be useful measures of treatment efficacy, as they remain detectable even in highly treated waters that only trigger minimal response specific, non-specific and reactive toxicity assays. The results also confirm the capability of advanced water treatment to produce very high quality of water.
Where ozonation and BAC were used, all of the tested final effluents produced only minimal biological response in the deployed bioanalytical tools. When biological activity was detected, it was always less than 10× above the assay quantification limit or activity in the ultrapure laboratory blank. This suggests that even in those cases where biological activity was detected in the final effluent, that activity is unlikely to be of significant health concern. Bioanalytical tools thus provide additional evidence that ozonation and BAC are effective technologies to produce high quality purified recycled water.
Microfiltration and ultrafiltration can be effective techniques to remove pathogens but they are not effective at removing trace organic contaminants82 or their associated biological response.32,73
There is a growing number of studies that have applied various in vitro bioassays in small-scale experiments to determine treatment efficacy,84–93 in particular because bioanalytical tools provide a measure of the total biological response. This can provide a considerable improvement over the commonly accepted method of conducting these tests, which only include chemical analysis of a select number of compounds. This standard type of analysis can show the removal of a specific chemical structure, but does not indicate whether potentially more toxic transformation products have formed during treatment. Applying standard chemical analysis for targeted compounds in combination with bioanalytical tools can overcome this limitation and provide a more comprehensive assessment of treatment efficacy. These bench-scale studies can provide a useful and comparatively cost-effective method to compare different treatment configuration allowing careful fine-tuning of the treatment train to minimize biological activity in the reclaimed water, as was done for example at the Tampa Water Resource Recovery Project (see above). A recent review of advanced oxidation processes in water and wastewater treatment strongly emphasized the need to combined chemical analysis with bioassay testing to detect toxic by-product formation from advanced oxidation processes.94In vitro methods effectively complement chemical analysis methods to provide a more comprehensive measure of treatment efficacy. For example, a recent study showed that while chemical analysis alone indicated that sand filtration was an effective method to polish wastewater from a Swedish wastewater treatment plant, bioassays clearly demonstrated that toxic compounds were present in sand filter effluent (even if the monitored compounds were not).88 This study highlights that conclusions from chemical analysis alone may incorrectly identify treatment options as suitable when they in fact produce toxic by-products.
In vitro bioassays are almost always conducted with concentrated water samples, which have been extracted either by liquid-liquid extraction (LLE) or solid-phase extraction (SPE). This means that inorganic species, highly water soluble organics, and highly volatile organic compounds are generally not entirely isolated in current extraction/concentration processes. Moreover, as compared to modern targeted analyses where surrogate standards are added to correct analytical data for losses and inefficient extraction,95,96 surrogates are not considered viable for bioassays due to the high potential to interfere with the biological responses. Extraction is generally carried out for two reasons: 1) to concentrate the organic constituents in water samples, and 2) to focus bioassay responses on the world of organic chemicals and not inorganic substances. Thus substances like bromate and perchlorate that are relevant to water reuse projects would not likely be detected by existing bioassay procedures, and bioassays are intrinsically susceptible to variability in extraction efficiency and/or procedure. Therefore, it is important to ensure that a suitable extraction technique is used that retains as wide a spectrum of chemical compounds as possible.73,97 However, it is impossible to say that the every single organic constituent is adequately extracted and concentrated during these processes.
Most cell lines used for bioassays are cancerous cell line, which (as opposed to primary cells) easily proliferate under laboratory conditions. Cancer cells can exhibit morphological and genetic differences compared to normal/healthy cells, and these need to be taken into account when analysing bioassay results. This is not a particularly significant issue when bioassays are used as detection tools for biologically active contaminants, but can be very relevant when bioassays are as representative tissues in a human hazard context.
The issue that has plagued bioanalytical methods for a very long time is what to do with a positive (or negative) bioassay result. There are currently no bioanalytical guidelines in drinking or recycled water regulation (although it should be noted that some dioxin guidelines are based on bioanalytical toxic equivalency, and that bioassays for dioxin-like activity, such as the DR-CALUX, have been used to provide a sum-measurement of all dioxin-like compounds in water). There is currently significant scientific effort to develop bioassay-based “guidelines”, commonly called “effects-based trigger values” (EBT) to highlight that these are not meant to be enforceable standards but rather screening levels that would trigger further conventional chemical analysis to identify causative chemicals and, if deemed necessary, effective treatment options. Brand et al.98 proposed several EBT for endocrine activity, as measured by several CALUX assays. Escher et al.69 has recently proposed a generic framework to derive EBT values for receptor-mediated pathways. Tang et al.29 and Escher et al.99 proposed an approach to derive EBT for non-specific assays, such as the Microtox assay and the oxidative stress response. Other projects are currently underway, such as the DEMEAU project funded by the European Commission, that aim to provide guidance on EBT. All of these proposals are still very novel, and require some time to be fully evaluated and tested by regulators before they can be more widely used.
One issue that is limiting greater uptake of bioanalytical methods is the lack of bioassay-based guidelines to compare bioanalytical results to. While there have been several proposals in this area, these still need to be evaluated by health regulators. However, it has long been recognized that at the very least bioanalytical tools can be used to compare alternative water supplies such as reclaimed water with current conventional drinking waters to give information on the toxic potential associated with different water supplies.15
It is important to keep in mind that adoption of bioanalytical tools for recycled water monitoring will most likely not lead to lower monitoring costs. The cost of testing samples in a thorough in vitro bioassay battery is equivalent to current chemical analysis costs. Bioanalytical tools do not replace chemical testing, but rather they present an important addition to our current monitoring strategies by providing a means to detect non-target chemicals and unexpected transformation products, and provide a sum measure of toxic chemicals acting via the same mode of action. However, recent developments in high-throughput testing are likely to lead to a reduction in the per sample cost of in vitro testing, and application of intelligent testing strategies combining a first screening (tier 1) stage with bioanalytical tools and suitable surrogate/indicator chemicals could lead to a reduction of total analytical costs associated with measurement of hundreds of chemicals.
(1) Assays for endocrine activity, in particular estrogenic and glucocorticoid activity. Reporter gene assays are exquisitely sensitive to hormonally active compounds, and provide a sensitive measure of potential endocrine disruption, which is of high public concern;
(2) While obviously not an issue specific to reclaimed water, it is important to continue to monitor disinfected water with assays for reactive toxicity such as mutagenicity and genotoxicity. Although the results from these assays have been and will continue to be difficult to fully comprehend without clearly identified causative chemicals, comparison with other water sources and drinking water provide an important context for the activity in reclaimed water. It is also important to understand the limitation of the current (mostly bacteria-based) assays for reactive toxicity in a human health perspective, and development of novel assays better able to detect human carcinogens should be encouraged;
(3) More difficult to connect to a health outcome at the moment (although future developments in molecular toxicology may fill in the gaps), adaptive response assays (particularly oxidate stress) and xenobiotic metabolism assays (particularly AhR and PXR pathways) appear highly sensitive to compound in both source and reclaimed waters.28 It is particularly important with these assays to compare the results with currently accepted water sources, as even highly treated water is likely to produce a biological response in those assays, which can respond to compounds that may not be toxic to whole organisms due to downstream defense and repair mechanisms.
(4) Finally, bacterial toxicity assays are more sensitive than cytotoxicity assays with human cells, although of course less relevant to human health assessment. Their sensitivity to a wide range of compounds29 may make them well suited as indicators of treatment, especially when applied online.
It should be noted that this list should not be seen as a comprehensive and final list, and future research may well identify other modes of toxic action that are relevant to drinking water.
Perhaps the most difficult question faced by scheme operators is what to do when a water sample produces a positive bioanalytical result. The studies presented in this review clearly highlight that this is not an unexpected outcome. This does not imply that the water is unsafe, but rather is a consequence of the exquisite sensitivity of some of the in vitro assays that detect early molecular or cellular events of the adverse outcome pathway. Decades of experience, however, suggest that bioassays can be used to provide an improved monitoring programme with clear operational implications. As a starting point, it is crucially important to set specific targets, or trigger levels, prior to applying bioanalytical tools. Where possible, these trigger levels should be based on sound toxicological methods. If a trigger level is not available for a specific bioassay, the target could simply be the bioassay response with current drinking water, which would ensure that the reclaimed water is at least as good as current drinking water. Once the trigger level has been established, a simple step-wise decision framework can be followed, as described for example in Fig. 2.
AChE | Acetylcholinesterase |
AOP | Adverse Outcome Pathway |
A-SCREEN | a bioassay for androgenicity based on inhibition of proliferation of breast cancer cells |
BAC | Biologically Activated Carbon |
CAR | Constitutive Androstane Receptor |
CHO | Chinese Hamster Ovary |
CPA | Cytokine Production Assay |
DEQ | Diuron Equivalent Concentration |
DHTEQ | Dihydrotestosterone Equivalent Concentration |
EBT | Effect Based Trigger value |
ECVAM | European Centre for the Validation of Alternative Methods |
EEQ | 17β-Estradiol Equivalent Concentration |
ERBA | Estrogen Receptor Binding Assay |
E-SCREEN | a bioassay for estrogenicity based on proliferation of breast cancer cells |
FCMN | Flow Cytometry Micronucleus; GAC = Granular Activated Carbon |
GSH | Glutathione |
GTU | Genotoxic Unit |
GWRS | Groundwater Replenishment Scheme |
I-PAM | Imaging Pulse Amplitude Modulation, a method to measure photosynthesis inhibition |
LDH | Lactate Dehydrogenase |
LLE | Liquid-liquid Extraction |
MF | Microfiltration |
MFO | Multifunction Oxidase |
MTT | a colorimetric assay for assessing cell metabolic activity |
NICEATM | National Toxicology Program Interagency Centre for the Evaluation of Alternative Toxicological Methods (US) |
NRC | National Research Council (US) |
NRU | Neutral Red Uptake |
OECD | Organisation for Economic Cooperation and Development |
PPAR | Peroxisome Proliferator-Activated Receptor |
PTEQ | Parathion Equivalent Concentration |
PXR | Pregnane X Receptor |
REF | Relative Enrichment Factor |
RO | Reverse Osmosis |
SPE | Solid Phase Extraction |
TCDDEQ | TCDD Equivalent Concentration |
TEQ | Toxic Equivalents |
TMXEQ | Tamoxifen Equivalent Concentration |
T-SCREEN | a bioassay for thyroid activity based on proliferation of rat pituitary cells |
TTEQ | Testosterone Equivalent Concentration |
TU | Toxic Unit |
UF | Ultrafiltration |
UV | Ultraviolet |
WCRWS | Western Corridor Recycled Water Scheme |
WIL2NS | a human B lymphocyte cell line |
WWTP | Wastewater Treatment Plant |
YAS | Yeast Androgen Screen |
YES | Yeast Estrogen Screen. |
This journal is © The Royal Society of Chemistry 2015 |