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A zebrafish scale assay to monitor dioxin-like activity in surface water samples

A zebrafish scale assay to monitor dioxin-like activity in surface water samples
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  PAPER IN FOREFRONT A zebrafish scale assay to monitor dioxin-like activityin surface water samples Sergi Pelayo  &  Ramón López-Roldán  & Susana González  &  Marta Casado  &  Demetrio Raldúa  & Jose Luis Cortina  &  Benjamin Piña Received: 25 May 2011 /Revised: 12 July 2011 /Accepted: 26 July 2011 /Published online: 6 August 2011 # Springer-Verlag 2011 Abstract  New regulations on water quality require a closecontrol of the possible biological activities known or unexpected pollutants may bring about. We present here a  protocol based on the direct exposure of zebrafish to river water and the analysis of expression of specific genes intheir scales to determine the presence of compounds withdioxin-like biological activity. The method does not requirethe killing of animals and allows detection of the biologicalactivity after a single day of exposure. When tested, themethod with real samples from the Llobregat River, clear temporal and spatial variations were observed, demonstrat-ing its suitability for monitoring natural variations in water quality linked to specific discharges. High biologicalactivities were unrelated to the currently checked water quality parameters (macropollutants, turbidity, TOC, etc.), but they did correlate with the presence of micropollutants(estrogens, detergents, etc.) related to domestic and/or industrial runoffs. The scale assay therefore provides a new tool to evaluate water quality changes that cannot beeasily derived from the existing standard analytical proce-dures. It ranks among the very few described protocols ableto detect biological effects from natural water samples,without a pre-concentration step, and after only 24 h of exposure. Keywords  Dioxine-like pollutants.Real-time PCR .  Daniorerio .Bioassays.RNA quantification.cyp1a .GC-MS Introduction Water quality regulations are becoming more stringent bothat national and international levels. In the European context, both the Environmental Liability Directive (2004/35/EU)and the Water Framework Directive (2000/60/EU) (WFD)respond to new paradigms, based on proactive approaches,rather than to legal restrictions, as the latter are hardly ableto cope with the directives of international environmentalagreements [1].The WFD, which is periodically updated (recently by2008/105/EU), requires a good ecological status of all thewater bodies. It requires monitoring the discharges in riversand other water bodies of priority and emerging micro- pollutants, in order to assess their impact on aquaticecosystems. Its last version defines a Priority SubstancesDirective in which Environmental Quality Standards aredefined for a list of 33 pollutants, although a morecomprehensive list is currently under consideration. How-ever, even large-scale analyses for these 33 pollutants todetermine whether or not their concentrations are below therespective EQ would not necessarily be representative of the water status. Moreover, spot sampling campaigns, themost common approach for analyzing these compounds,are costly and labor-intensive and not sufficient to have anaccurate picture of the chemical and biological status of water quality [2  –  4]. S. Pelayo :  M. Casado :  D. Raldúa  : B. Piña ( * )Department of Environmental Chemistry, IDAEA-CSIC,Jordi Girona 18-26,08034 Barcelona, Spaine-mail: bpcbmc@cid.csic.esR. López-Roldán :  S. González : J. L. Cortina CETaqua, Water Technology Center,Carretera d ’ Esplugues, 75, Cornellà,08940 Barcelona, SpainJ. L. Cortina Department of Chemical Engineering,Universitat Politècnica de Catalunya (UPC),Diagonal 647,08028 Barcelona, SpainAnal Bioanal Chem (2011) 401:1861  –  1869DOI 10.1007/s00216-011-5288-5  For all of these reasons, new tools should be estab-lished to obtain all the information needed. Bioassaysconstitute a fundamental component of any decision-making process concerning the evaluation of water quality. We present here a bioassay devoted to detect changes or fluctuations in chemical concentration of specific pollutants in surface waters, as those resultedfrom example for accidental spills. This bioassay relies onthe known ability of fish scales to rapidly respond tochemical pollution by rising the expression levels of CYP1A mRNA, and on existent methodologies to analyzethis increase at relatively low costs in terms of time, labor,and money [5].Cytochrome P450 1A (CYP1A) is an established biomarker of exposure to toxicants in many animal species,including fish [6  –  8]. CYP1A expression increases as a response to the presence in the blood of ligands of the arylhydrocarbon receptor (AhR), which include a variety of  pollutants, such as 2,3,7,8-tetrachlorodibenzo(  p )dioxin and benzo[a]pyrene (B[a]Py). The presence of these substances,globally known as dioxin-like pollutants, has been relatedto different deleterious effects, including immune dysfunc-tion, endocrine disruption, reproductive toxicity, develop-mental defects, and cancer in vertebrates [9  –  11].Changes on CYP1A activity have been usually evaluated by measuring one of its associated enzymatic activities,such as the ethoxyresorufin  O -deethylase activity (EROD;[12, 13]), although analysis of CYP1A gene expression by mRNA-quantification methods are recently becoming suit-able alternatives [7, 14, 15]. These methods are specially useful for in-field studies due to possibility to stabilizemRNA with appropriate agents and the small amount of sample required for the analysis [16, 17]. Whereas both EROD assays and most mRNA-based methods usuallyimplicate dissection of internal organs (liver, kidney, ovary,etc.) or a significant damage of the specimen (biopsy, gillremoval, etc.), monitoring toxicant exposure in fish scalesis a non-destructive method that has many applications inenvironmental monitoring and food safety control [5]. Fishscales are metabolically active, containing different bonecells similar to bone osteoclasts and osteoblasts in tetra- pods. These cells respond to a variety of physiological andexternal effectors, including calcitonin, melatonin, estro-gens, and heavy metals [18  –  21]. We present here a modification of the published non-lethal bioassay basedon goldfish ( Carassus auratus ) scales [5], specificallydesigned to monitor freshwater quality. We used thezebrafish  Danio rerio  to reduce up to 90% the requiredvolume of water samples and the aquarium space anddemonstrated that the method is able to detect naturalchanges in water quality in a direct exposure scheme,without pre-concentration of the organic compounds present in the water. Materials and methods Sampling sites and sampling procedureLlobregat River is located in north east of Spain, with a 160-km-long course and discharging into the Mediterranean Sea,10 km south of Barcelona. The Mediterranean climate, predominant in the Llobregat basin, is characterized byvariable flows that can range from low m 3 /s to severalhundred m 3 /s in storming periods, normally in spring andfall. Despite this relative low flow values and its impredict-ability, the Llobregat basin constitutes the most important drinking water source for Barcelona and its surrounding area. Not surprisingly, the whole basin is overexploited and polluted by the effluents from more than 30 urbanwastewater treatment plants (WWTP), industries, and agri-culture runoffs, particularly at the lower course. To enhancethe water quality, several bypass channels have beenconstructed along the river in order to avoid the arrival of the most contaminated fractions to drinking water treatment  plants (DWTP), including effluents from tannery, food products, textile, pulp and paper industries, among others,as well as agricultural runoffs (see Fig. 1). These bypasschannels are discharged again into the Llobregat River after the catchment for the DWTPs increasing the river flow but worsening water quality at the last section of the river.Twenty-four surface water samples were collected at threedifferent sites in the river basin (depicted in Fig. 1): site 1 is a DWTP intake point located downstream of the town of Esparraguera (22,000 inhabitants), receiving the effluent WWTP of this municipality, and from other towns as Abrera (11,500 inhabitants), Olesa de Montserrat (23,600 inhabi-tants), Collbató (4,200 inhabitants), and El Bruc (2,000inhabitants), among others. This point has the impact of textile, chemical surface treatment, and other industries. Site2 is also a DWTP intake point located at approximately30 km from site 1, in the lower part of the river, and its water quality is influenced by different discharges and tributaries aswell as by the impact of drainage system overflows. Site 3lies just downstream to site 2, after the confluence of the bypass channels to the main river course.Samples were collected in two campaigns, one in spring(7th  –  18th June 2010) and a second in the fall (21st October to 4th November 2010). In both cases, site 2 was sampled,along with a second site, site 1 in spring and site 3 in thefall. Surface water samples were collected in amber glass bottles and transported to the laboratory, where they werekept refrigerated (4 °C) until their use.Water quality analysisQuality parameters and pollutants were analyzed in all thewater samples. Physicochemical parameters determined, 1862 S. Pelayo et al.  theirmethodofanalysis,limitofdetection(LOD),andrangeof concentrations found are listed in Table 1. These parameterswere only determined at site 2 for both sampling campaigns.A total of 24 pollutants, belonging to the classes of  polycyclic aromatic hydrocarbons (PAHs), polychlorinated biphenyls (PCBs), alkylphenols, plasticizers, and estrogenswere measured in water samples by gas chromatography  –  mass spectrometry. The analytical method is certified by theSpanish Accreditation Body (ENAC: web/english/home) with accreditation number 109/LE285.The LODs were 10 ng/L for all PAHs analyzed, 20 ng/L for PCBs, 100 ng/L for alkylphenols, 20 ng/L for the plasticizer, and 50 ng/L for the estrogens. Table 2 listscompounds analyzed in this work.Biological assay  Exposure protocol  Ten 1-year-old  D. rerio  males were exposed to water samples in 5,000 mL open, mechanically aired PYREXcontainers for 24 h at 25 °C. Two subsets of fish wereexposed to Aquarium water (1.125 g/L Instant Ocean®+250  μ  g/L CaSO 4 ) containing either 1  μ  M of ß-naphtho-flavone (using dimethyl sulfoxide (DMSO) as vehicle), or only DMSO, as positive and negative controls, respectively.Mortality during the exposure protocol was anecdotal. Scale collection Fish were treated with anesthesic Fenoxiethanol (1:2,000 inAquarium water) to minimize fish stress. Fenoxiethanolaction is completely reversible. Three scales were removedfrom the front-dorsal area, as this number was considered asthe maximal not inducing relevant fish lethality. After scaleextraction, fish recovered in 1 to 2 weeks, although their suitability for reuse has not been formally evaluated yet.  RNA extraction and whole transcriptome amplification Removed scales were preserved in RNAlater® (Sigma-Aldrich, St. Louis, MO) to prevent RNA damage. TotalRNAwas extracted using the Qiagen RNAeasy® Micro Kit.Quality and quantity of resulting RNA were measured by both micro-UV spectrophomotery (Nanodrop) and micro-fluidic electrophoresis (Bioanalyzer, Agilent Technologies).In the next step, we used a cDNA amplification protocolusing the Takara CellAmp whole transcriptome amplifica-tion (WTA) Kit® and Takara Ex Taq Hot Start Version®.This protocol is designed to perform cDNA amplificationdirectly from small amounts of cell and also from smallamount of RNA. Amplified cDNAwas diluted according toexpected amounts of target genes and used as template inreal-time PCR experiments. The WTA protocol amplifiescDNA by approximately 1,000-fold, and we tested that it  Fig. 1  Map of the sampling area at the Llobregat River basin (NE Spain). Geographical locations of sampling points, wastewater treatment plants( WWTP  ), drinking water treatment plant (  DWTP  ), and the path of Llobregat River, its tributaries and bypass channels are indicatedA zebrafish scale assay to monitor dioxin-like activity 1863  did not change significantly the relative proportion of specific cDNA molecules in zebrafish scale samples (to be published elsewhere). Quantitative real-time PCR Primers for   ef1 α  (reference gene, GeneBank accessionnumber X77689) and  cyp1a  (  D. rerio  CYP1A gene, dioxin-like response, GeneBank accession number AB078927) for cyprinids have been published elsewhere [5, 22]. Amplifica- tion of all sequences was tested by conventional and qRT-PCR (Lightcycler, Roche). Relative mRNA abundances of different genes were calculated from the second derivativemaximum of their respective amplification curves (Cp;calculated by triplicates). To minimize errors on RNAquantification among different samples, Cp values for thetarget genes (Cp tg ) were normalized to the average Cp valuesof the reference gene to obtain the corrected Cp values (corr Cp=Cp tg  –  Cp ref  ). To facilitate the interpretation of graphs,corr Cp values were transformed into mRNA copies per 1,000 copies of   ef1 α  mRNA ( ‰  of reference gene)according to the equation 1,000×2 − corrCp [23].Data treatment and statistical analysesDatasets were checked for outliers calculating thecorresponding  Z  -scores; data points (individual Cp values)with  Z  -scores of >2 were removed from the final datasets (11samples from a total of 265 (4.2%)). Correlations betweendifferent parameters were analyzed with the SPSS 19 package (SPSS Inc., Chicago, Il). Non-parametric Spear-man ’ s correlation was chosen to correlate disparate sets of data (physicochemical data, concentrations, and gene expres-sion values). Statistical treatment of gene expression between Table 2  LOD values and maximal (MAX), average (AVG), and frequency (FREQ) values for different pollutants in Llobregat water samplesCompound LOD( μ  g/L)Site 1 (samplingcampaign 1,  n =6)Site 2 (samplingcampaigns 1 & 2,  n =12)Site 3 (samplingcampaign 2,  n =6)Total FREQ(%)MAX( μ  g/L)AVG( μ  g/L)FREQ(%)MAX( μ  g/L)AVG( μ  g/L)FREQ(%)MAX( μ  g/L)AVG( μ  g/L)FREQ(%)Alkylphenols Nonylphenol diethoxilate 0.1 b.d.l. b.d.l. 0 0.31 0.57 25 1.6 0.74 50 25 Nonylphenol monoethoxilate 0.1 b.d.l. b.d.l. 0 0.26 0.21 17 2.7 0.97 50 21 Nonylphenol (CAS 104-40-5) 0.1 0.44 0.25 50 1.2 0.38 50 6.2 1.67 83 584- Tert  -octylphenol 0.1 b.d.l. b.d.l. 0 b.d.l. b.d.l. 0 0.15 0.13 33 8Plasticizer Bisphenol A 0.02 0.1 0.06 50 0.13 0.076 42 0.04 0.035 33 42Estrogens β -Estradiol 0.05 0.13 0.11 33 0.12 0.1 25 b.d.l. b.d.l. 0 21Estriol 0.05 b.d.l. b.d.l. 0 b.d.l. b.d.l. 0 0.17 0.13 50 13Estrone 0.05 b.d.l. b.d.l. 0 0.56 0.56 8 0.44 0.23 67 21 b.d.l.  below detection limit Parameter Method of analysis LOD Min  –  max (mean)Flow (m 3 /s) Flowmeter 4.2  –  111.8 (25.7) a   pH Electrometry 7.6  –  8.8 (8.1)Temperature (°C) Thermometry 17  –  26 (20.5)Turbidity (NTU) Turbidimetry 0.2 26  –  1800 (269)UVabsortion 245 nm/100 cm Spectroscopy 7.9  –  22.5 (13)Conductivity ( μ  S/cm) Potentiometry 3 590  –  2,719 (1,390)Total alkalinity (mg CaCO 3 /L) Automatic acid  –   base titration 146  –  404 (246) NH 4+ (mg NH 4+ /L) Ion chromatography 0.05 <0.05  –  34 (0.5)Total organic carbon (mg/L) IR spectroscopy 0.2 3.2  –  9.9 (4.1)Dissolved oxygen (mg O 2 /L) Oximetry 6.1  –  8.9 (10.0) NO 2 − (mg NO 2 − /L) Ion chromatography 0.04 0.1  –  0.7 (0.4) Table 1  Physicochemical parameters determined at site 2(both sampling campaigns) a  Data obtained from Agència Catalana de l'Aigua 1864 S. Pelayo et al.   pairs of values (treated vs. control) was done by the Student  ’ s t   test; analyses of values from different populations (sampledsites) were performed using one-way ANOVA, after assessment of normality of data by the Kolmogorov  –  Smirnov test. Results and discussion Analysis of   cyp1a  expression in zebrafish scalesExposure to 1  μ  M of ß-naphthoflavone for 24 h increased cyp1a  mRNA levels in zebrafish scales by about 100-fold(Fig. 2, left panel, mean the logarithmic scale). This value issimilar to the value observed for goldfish, and demonstratesthe feasibility of the method [5]. DNA sequence of theamplified fragment was identical to the known  cyp1a  genesequence from  D. rerio  (data not shown). Three indepen-dent experiments of   cyp1a  induction in zebrafish scales byß-naphthoflavone were performed using different fish poolsand reagent batches within a period of about 6 months. Afourth similar experiment was analyzed without WTAamplification, by extracting a large number of scales andcorrecting the amount of input RNA according to theexpected amplification of WTA-treated samples. Table 3shows the statistical parameters of the results from theseexperiments. Cp values from reference gene  elf1 α  showed a moderate variability among experiments, with a coefficient of variation slightly above 10% for the 62 samples, but nosignificant changes between treated and non-treated sam- Fig. 2  Relative  cyp1a  expression values (expressed as  ‰  of referencegene) in zebrafish scale. The  right panel   ( Controls ) shows control (yellow triangles ,  green line ) and naphthoflavone-treated (  purplecircles ,  red line , 1  μ  M, 24 h) zebrafish for four independent experiments, totaling 62 individual data. Note that one experiment was performed without WTA amplification (rightmost datapoint). Central and right panels , results from fish exposed to water samplesfrom site 1 ( blue diamonds ), site 2 (  green circles ), or site 3 ( orange squares ), from both Spring ( center  ) and Fall ( right  ) campaigns. Notethat samples from site 2 were collected at both campaigns.  Whiskers indicate SD values;  asterisks  indicate significant differences fromnegative controls (Student's  t   test: *  p <0.05; **  p <0.01; ***  p <0.001) Table 3  Statistical parameters for qRT-PCR results from WTA-amplified and non-amplified samplesSample subset Gene Parameter All Amplified samples Non-amplified samples  T   test (treated vs. control)Average SD  n  Average SD  n  Average SD  n  Amplified Non-amplifiedAll  elf1a  Cp 14.56 1.61 62 14.70 1.71 52 13.81 0.36 10Control  elf1a  Cp 14.32 1.56 28 14.42 1.69 23 13.85 0.43 5 cyp1a  Cp 23.66 1.89 28 23.79 2.06 23 23.06 0.50 5corr Cp 9.34 1.54 28 9.37 1.69 23 9.21 0.52 5Treated  elf1a  Cp 14.75 1.64 34 14.92 1.72 29 13.77 0.34 5 >0.05 >0.05 cyp1a  Cp 16.97 1.55 34 17.20 1.53 29 15.60 0.71 5 6.0×10 − 18 5.6×10 − 8 corr Cp 2.21 0.82 34 2.28 0.85 29 1.83 0.55 5 3.2×10 − 25 2.1×10 − 8 A zebrafish scale assay to monitor dioxin-like activity 1865
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