- Research article
- Open Access
Degradation of progestagens by oxidation with potassium permanganate in wastewater effluents
© Fayad et al.; licensee Chemistry Central Ltd. 2013
- Received: 15 February 2013
- Accepted: 10 May 2013
- Published: 15 May 2013
This study investigated the oxidation of selected progestagenic steroid hormones by potassium permanganate at pH 6.0 and 8.0 in ultrapure water and wastewater effluents, using bench-scale assays. Second order rate constants for the reaction of potassium permanganate with progestagens (levonorgestrel, medroxyprogesterone, norethindrone and progesterone) was determined as a function of pH, presence of natural organic matter and temperature. This work also illustrates the advantages of using a novel analytical method, the laser diode thermal desorption (LDTD-APCI) interface coupled to tandem mass spectrometry apparatus, allowing for the quick determination of oxidation rate constants and increasing sample throughput.
The second-order rate constants for progestagens with permanganate determined in bench-scale experiments ranged from 23 to 368 M-1 sec-1 in both wastewater and ultrapure waters with pH values of 6.0 and 8.0. Two pairs of progestagens exhibited similar reaction rate constants, i.e. progesterone and medroxyprogesterone (23 to 80 M-1 sec-1 in ultrapure water and 26 to 149 M-1 sec-1 in wastewaters, at pH 6.0 and 8.0) and levonorgestrel and norethindrone (179 to 224 M-1 sec-1 in ultrapure water and 180 to 368 M-1 sec-1 in wastewaters, at pH 6.0 and 8.0). The presence of dissolved natural organic matter and the pH conditions improved the oxidation rate constants for progestagens with potassium permanganate only at alkaline pH. Reaction rates measured in Milli-Q water could therefore be used to provide conservative estimates for the oxidation rates of the four selected progestagens in wastewaters when exposed to potassium permanganate. The progestagen removal efficiencies was lower for progesterone and medroxyprogesterone (48 to 87 %) than for levonorgestrel and norethindrone (78 to 97%) in Milli-Q and wastewaters at pH 6.0-8.2 using potassium permanganate dosages of 1 to 5 mg L-1 after contact times of 10 to 60 min.
This work presents the first results on the permanganate-promoted oxidation of progestagens, as a function of pH, temperature as well as NOM. Progestagen concentrations used to determine rate constants were analyzed using an ultrafast laser diode thermal desorption interface coupled to tandem mass spectrometry for the analysis of water sample for progestagens.
- Potassium permanganate
- Steroid hormones
- Endocrine disruptors
- Kinetic rate constant
Many endocrine-disrupting compounds (EDCs), such as steroid hormones (SH) have been detected in waste and surface water matrices [1–4]. They originate from naturally-occurring (e.g. normal urine excretion of estrogens from mammals) and synthetic (e.g. progestagens in oral contraceptives and hormone replacement therapy) sources. There has been growing concerns towards EDCs’ effects on the reproductive physiology of wildlife populations at very low concentrations, i.e. from 0.1 to 1.0 ng L-1[5–7]. Given their strong endocrine-disrupting potency and their occurrence, selected estrogens (estradiol, estrone and 17-α-ethinylestradiol) and progestagens (progesterone, levonorgestrel, medroxyprogesterone and norethindrone) have been targeted and detected in wastewater, surface water and drinking water [8–14].
Although the impact of natural and synthetic estrogens has been well documented, only a limited number of studies have been conducted on the ecotoxicological and environmental risk related to progestagens [15, 16]. Progestagens are steroid hormones that produce effects similar to those of progesterone, a C-21 steroid hormone involved in the female menstrual cycle, pregnancy and the embryogenesis of humans and other species . Several synthetic progestagens have been developed, given that natural progesterone is very rapidly inactivated in the human body. Synthetic progestagens can have various hormonal activities, such as estrogenic, anti-androgenic and androgenic . Their presence in wastewater treatment plant (WWTP) effluents can pose a risk for the aquatic environment given their potential for impact on the reproductive success and the chemoreception of fish [18, 19]. Synthetic progestagens were first developed and used in the 1960s as an effective method for contraception . In Europe and America, the consumption rates of synthetic progestagens ranks as the first among all contraception methods, i.e. 33% in the United States and as high as 58% in some European countries . In the United Kingdom, the estimated yearly usage of progestagens from oral contraception (~1723 kg/year) is higher than that of estrogens and androgens combined (~706 kg/year) . In addition, the environmental amounts of progestagens and androgens excreted via urine is estimated to be 100 to 1000 times higher than that of estrogens in humans . Therefore, progestagenic steroid hormones will be discharged into environmental waters from WWTP effluents and such releases should be better documented.
Several studies conducted in numerous countries [9, 12, 17], have shown that WWTP effluents and receiving water bodies contain sufficient amounts of progestagenic compounds to induce harmful effects on fish, with their concentrations varying from 0.2 to 205 ng L-1 for progestagens in wastewater samples [12, 17, 23]. With growing populations and increased discharge from WWTPs, the presence of progestagens in surface waters could be a cause for concern for drinking water treatment plants and therefore improved removal methods should be explored since conventional treatment methods have proven to be inadequate.
In contrast to other oxidants such as chlorine and ferrate (VI), permanganate is effective over a wide pH range and can control the formation of trihalomethanes and other disinfection by-products [30, 31]. In addition, permanganate will generate an insoluble environmentally benign reduction product (MnO2(s)), which can enhance coagulation and simultaneously adsorb trace metals before their removal by sedimentation/filtration [27, 32, 33]. Previous work has established rate constants for selected estrogens (estradiol, estriol and estrone) using potassium permanganate, with values ranging from 16 to 38 300 M-1 s-1 at pH 5.0 to 12 [24, 26]. Currently, no published information for the removal of progestagens by potassium permanganate is available. Progestagens should have different reactivity towards permanganate due to the absence of a phenolic moiety in their structures as compared to the estrogens.
Based on geology, climate, human influence and the surrounding watershed, different water sources will contain variable amounts of natural organic matter (NOM) with different characteristics, such as high and low molar mass organic material [34–36]. During the past 20 years, a significant increase in NOM concentrations has been observed in several surface water sources worldwide [37–40]. Permanganate has been shown to react with NOM compounds and should be considered when evaluating reaction rate constants [26, 28]. The operation of water treatment facilities will therefore be influenced by NOM, since it can interfere with the oxidation removal of other contaminants by competitive consumption . The impact of temperature (an especially relevant parameter for water utilities spawning their operation over four distinct seasons) and the dissolved fraction of NOM on kinetic rates have not yet been studied for the oxidation of progestagens with potassium permanganate.
To date, all analytical procedures used to determine oxidation rate constants for EDCs and steroid hormones have included the use of chromatography (liquid or gas) coupled to tandem mass spectrometry (MS/MS), ultraviolet or diode array detection . Fayad et al. (2010) developed a sensitive method enabling high-throughput sample analysis of eight selected steroid hormones using a novel sample introduction method, LDTD-APCI coupled to MS/MS. The analysis time is achieved in seconds (<10 sec) compared to several minutes using the more traditional chromatography methods. As a result, the identification and quantification of the studied compounds will be much faster, the total analysis cost will be reduced and sample throughput will be significantly increased.
The objectives of this study were to: i) determine the rate constants for the reaction of potassium permanganate with progestagens (levonorgestrel, medroxyprogesterone, norethindrone and progesterone) in pure water and wastewater effluents using laboratory bench-scale assays, ii) evaluate the influence of operating conditions, i.e. pH, presence of NOM and temperature, on permanganate rate constants, iii) assess the validity of the determined rate constants when permanganate oxidation is applied to wastewaters. Furthermore, this work illustrates the advantages of using a novel analytical method, the LDTD-APCI-MS/MS apparatus, which is an alternative approach to chromatographic methods. This analytical approach facilitates the implementation of large experimental designs that require the evaluation of many different conditions and various time intervals. This method has allowed us to realize a quick determination of oxidation rate constants, while lowering analysis cost (no chromatography system is necessary) and increasing sample throughput. To the best of our knowledge, this paper presents the first results on the permanganate-promoted oxidation of steroid hormones without aromatic moieties, i.e. progestagens, as a function of pH, temperature as well as NOM levels.
The selected steroid hormones (levonorgestrel (LEVO), medroxyprogesterone (MEDRO), norethindrone (NORE) and progesterone (PROG)) used for this study are listed in Additional file 1: Table S1 with their molecular structures presented in Additional file 1: Figure S1. All progestagen standards (purity ≥ 97%) were purchased form Sigma Aldrich (St. Louis, MO). Isotopically-labeled 17α-ethinylestradiol, [13C2]-EE2, was used as an internal standard (IS) and obtained from ACP Chemical Inc. (Montreal, QC, Canada). Other chemicals, including potassium permanganate (KMnO4), potassium phosphate (monobasic and dibasic) and ascorbic acid were of analytical grade and used without further purification. All solvents used were of HPLC grade purity from Fisher Scientific (Whitby, ON, Canada) and ultrapure water (18 MΩ cm) used was produced with a Milli-Q (Millipore, USA) apparatus.
Individual steroid hormone stock solutions were prepared in methanol (MeOH) at a concentration of 1000 mg L-1 and kept at −20°C in amber vials for a maximum of three months. A mixed steroid hormone working solution was prepared prior to the experiments at a concentration of 200 mg L-1 by dilution in MeOH of individual stock solutions aliquots for spiking solutions at the desired concentrations. Phosphate buffers of pH 6 and 8 (final concentrations: 50 mM) were prepared by dissolution of the commercial compounds in water. Potassium permanganate working solution (5.638 mmol L-1), ascorbic acid working solution (65.68 mmol L-1) and other reagents were also freshly prepared in Milli-Q water prior to the experiments and stored in amber bottles at 4°C.
Water quality characterization
For the laboratory bench-scale experiments, wastewater effluents samples were taken from the water outlet of two municipal WWTPs in the province of Quebec, Canada. The first, WWTP A produces water with a DOC of 2.3 mg C L-1, an alkalinity of 80 mg CaCO3 L-1, UV absorbance (at 254 nm) of 0.027 cm-1, and a pH of 8.24. The second, WWTP B, produces water with a DOC of 7.7 mg C L-1, an alkalinity of 27 mg CaCO3 L-1, UV absorbance (at 254 nm) of 0.047 cm-1, and a pH of 6.30. Wastewater samples were not adjusted for pH and oxidation was carried out at ambient pH. The water samples were not analyzed for steroid hormones prior to oxidation experiments since their concentrations are orders of magnitude lower than the concentration spiked during the bench-scale experiments, as previously documented . The water samples were collected in 10 L polypropylene carboys washed and rinsed successively with distilled and ultrapure water (Milli-Q). Wastewater effluent samples were filtered (0.45 μm polyethersulfone) and kept at 4°C prior to the oxidation experiments. Prior to DOC analyses, samples were passed through pre-rinsed (1 L ultrapure water) 0.45 μm cellulose nitrate Supor-450 membrane filters (PALL Life Sciences, USA). DOC measurements were made using a 5310C total organic carbon analyzer (Sievers Instruments Inc., USA).
The validation and optimization parameters of the LDTD-APCI-MS/MS method used for the detection and quantification of the selected steroids were previously described . Briefly, water samples recuperated from the bench-scale oxidation experiments were first spotted (2 μL) into the LazWell 96-well polypropylene plate cavities and then left to dry (in a forced air oven at 30°C). Upon operation, a glass transfer tube is inserted into a well by an air-powered piston to avoid any sample loss. An infrared (IR) laser diode (980 nm, 20 W, continuous) is then focalized to impact the back of the metal inserts, thermally desorbing the dried sample which is vaporized into the gas phase. The uncharged analyte molecules travel along the transfer tube by a carrier gas to eventually reach the corona region for ionization by APCI and then be transferred to the MS inlet . The MS/MS parameters for the selected steroid hormones are presented in Additional file 1: Table S2. Further details of the theory and principles behind the LDTD (Phytronix Technologies, Quebec, QC, Canada) are provided in the SI (Text S1).
In the kinetic experiments, permanganate was analyzed at 515 nm with a spectrophotometer (Varian-Cary 100, Victoria, Australia) in a 1-cm quartz cell, by the N, N-diethyl-p-phenylenediamine (DPD) colorimetric method .
Laboratory bench-scale experiments
Oxidation experiments with potassium permanganate were conducted in 500 mL amber bottles (Fisher Scientific, Whitby, ON, Canda). All reactor assays were performed in duplicates. For ultrapure water (Milli-Q) samples, the pH was adjusted to 6.0 and 8.0 using the appropriate buffered phosphate solutions prior to the oxidation tests. It has been reported that phosphate buffers can enhance oxidation by permanganate of a certain number of phenolic compounds (i.e. triclosan, phenol, 2,4-dichlorophenol [46, 47]). This is in contrast with several other studies performed on non-phenolic and phenolic compounds alike (e.g. chlorinated ethylenes, microcystins and carbamazepine) where phosphate buffer had no reported impact on oxidation mechanisms using permanganate [27, 30, 48]. There are no reported studies in the literature that would suggest that progestogenic-like steroid hormones (non-phenolic) would be influenced by the addition of phosphate buffer for permanganate oxidation. For WWTP A and WWTP B effluents samples, buffered solutions were not necessary since their natural pH values were 8.24 and 6.30, respectively. Phosphate buffers were only used for the assays using ultrapure water. The pH values in the reactors were constant throughout the oxidation tests with changes between the initial and final pH not exceeding 0.2.
In order to perform the oxidation experiments at different temperatures (from 5 ± 2°C to 30 ± 2°C), the reactors were placed in a temperature-controlled water bath. The initial concentrations of steroid hormones spiked in the reactors ranged from 0.883 to 9.76 μM, with 17 to 53 μM of permanganate added for the oxidation tests. Aliquots of 1.8 mL were collected at specific time intervals into a 2 mL amber vial containing a stoichiometric ratio of ascorbic acid to immediately quench the residual permanganate. It was previously established that ascorbic acid was suitable to quench oxidant residuals during sampling, while not affecting the stability of the studied ECDs . Samples were then analyzed by LDTD-APCI-MS/MS to determine the residual concentration of steroid hormones.
The solvent used for the dissolution of the steroid hormones spiked in the reactors was MeOH. Initial tests were performed with acetonitrile and MeOH to assess their impact on permanganate decay rates in reactors with ultrapure water (without steroid hormones). Using MeOH showed that there was no decrease of initial permanganate concentration for up to 60 min contact times (Additional file 1: Figure S3). Reactor blank experiments (no steroid hormones added) for both wastewaters with the addition of permanganate were also conducted. All rate constants were determined under pseudo-first-order conditions, with permanganate in excess, in a batch reactor in ultrapure and wastewaters at pH 6.0-8.2.
Determination of rate constants for the reaction potassium permanganate
where C = oxidant residual (mg L-1); Co = initial oxidant residual (mg L-1) determined from the exponential fit of the relation between the oxidant residual and the time (min); k’ = oxidant first-order decay constant (min-1).
Permanganate decay in ultrapure and wastewaters
First-order apparent rate constants ( k , sec -1 ) for permanganate decay with and without progestagens in wastewaters at 22 ± 2°C for pH 6.3 (WWTP B, DOC 7.7 mg C L -1 ) and 8.2 (WWTP A, COD 2.3 mg C L -1 ) a
0.57 ± 0.02
0.44 ± 0.06
1.2 ± 0.1
1.13 ± 0.07
1.1 ± 0.2
1.0 ± 0.2
Oxidation of steroid hormones
Steroid hormone (SH) oxidation rate constants ( k , M -1 sec -1 ), removal efficiency (%) between 10 and 60 min and half-lives ( t 1/2 , min) derived from oxidation experiments using permanganate in Milli-Q and wastewaters (WWTP A, pH 8.2, DOC 2.3 mg C L -1 and WWTP B, pH 6.3, COD 7.7 mg C L -1 ) at 22 ± 2°C for pH 6.0 and 8.0 a
179 ± 10
199 ± 6
89 ± 12
89 ± 12
180 ± 5
302 ± 9
97 ± 8
90 ± 1
73 ± 2
80 ± 2
57 ± 20
58 ± 12
49 ± 2
159 ± 4
71 ± 1
87 ± 4
219 ± 13
224 ± 8
90 ± 11
78 ± 3
257 ± 10
368 ± 11
96 ± 2
92 ± 1
28 ± 2
23 ± 1
48 ± 11
41 ± 5
26 ± 2
109 ± 4
58 ± 3
80 ± 20
Table 2 also shows that pH did not have an impact on rate constants for progestagens either in ultrapure or wastewater effluents. This was expected since these compounds do not present any acid or basic character with predicted pKa values between 17.0 and 19.3 for LEVO, NORE and MEDRO (Additional file 1: Table S1). The influence of dissolved organic matter was also investigated by using effluent wastewaters with different levels of NOM (WWTP A with 2.3 mg C L-1 and WWTP B with 7.7 mg C L-1) and conducting the oxidation experiments at ambient pH. With aromatic moiety being one of the main predicted sites of attack for permanganate, a competition effect is possible with background components in waters that contain electron rich moieties, such as humic acids . Figure 1a and 1c as well as Table 2, show that at pH 6 the presence of NOM, regardless of the concentration present, did not have a significant effect on the rate constants with permanganate for LEVO, NORE and PROG (e.g. 179 to 180 M-1 sec-1 for LEVO, in Milli-Q (pH 6.0) and effluent waters (WWTP B, pH 6.3). On the other hand, oxidation of MEDRO was limited in effluent waters at pH 6.3. At higher pH, the presence of NOM systematically improved the efficiency of the oxidation of progestagens, as illustrated in Figure 1b and 1d as well as in Table 2.
Several ligands such as phosphate buffer, EDTA, and humic acid, have been shown to exert pH-dependent oxidation enhancement of phenolic compounds (Jiang et al. 2009) supporting the hypothesis of a catalytic role produced by the aqueous manganese intermediates (Mn(INT)aq) which are seemingly stabilized by metal-binding ligands . This was illustrated with an enhancement of the oxidation of phenolic compounds that was also noted for the presence of NOM in river water and wastewaters and attributed to the formation of such unidentified Mn(INT)aq species with a pH dependency of the rligand up to pH 9 .
The different trends observed in our data may reflect the fact that the role of ligands in Mn-promoted oxidation is closely related to the structure of the target organic molecules, as proposed by Jiang et al. . A significant improvement of oxidation of phenolic compounds using humic acids of various origins has been reported [46, 47, 52]. One could hypothesize that the presence of NOM in this case also contributes to enhance the oxidation of the progestagens. Hu et al.  have attributed the degradation efficiency of the oxidation of carbamazepine in the presence of permanganate to an electrophilic attack, the stabilization of Mn(INT)aq could also help improve this electrophilic attack onto the molecules of progestagens. In the case of our target compounds, NOM did not enhance oxidation at a pH 6.3 while a significant and consistent enhancement was noted at pH 8. Hu et al. did not observe any enhancement of carbamazepine oxidation at pH 5, 6 and 7 in the presence of 10 and 20 mg L-1 of humic acids . Within our dataset, it is difficult to fully dissociate what proportion of the difference in efficiency between pH values of 6 and 8 is attributable to an effect due an unknown difference in the chemistry of both effluent wastewaters tested. With the presumption that the effect is solely attributable to the pH difference, the nature of the NOM as a function of pH could also partly explain the observed results.
Dissolved humic substances have been known to influence removal of organic compounds from municipal and industrial wastewaters [53, 54] as well as being responsible for capturing and transporting both nonpolar (such as p,p’-DDT, 2,4,5,2’,5’-PCB and 2,4,4’-PCB) and polar (pesticides) contaminants [55, 56]. This could be a result of the humic macromolecules that have been shown to be densely coiled at lower pH values, such as that of the WWTP B (pH = 6.3) effluent (Figure 1a and 1c) for progestagens, as depicted by the random coil model . Therefore, i) the affinity of NOM to complex and stabilize Mn(INT)aq is lowered and the resulting catalytic activity is no longer observed and ii) progestagens (log Kow ≥ 2.97, Additional file 1: Table S1) could be complexed by the humic macromolecules in their hydrophobic structural voids cavities  making them less available for oxidation by permanganate. Inversely, at more alkaline pH, such as that of the WWTP A (pH = 8.2) effluent (Figure 1b and 1d) for progestagens, there is formation of negatively charged carboxyl groups found in the humic macromolecules. This induces mutual repulsion and expansion of the formerly coiled macromolecules , making them more flexible and slightly more polar in nature, thus promoting its reactivity allowing for the formation of more stable Mn(INT)aq compounds while reducing the progestagens affinity with the NOM. The impact of the structure of the target compound, the nature of the ligand and the pH dependency of NOM on the kinetics of permanganate oxidation needs to be further investigated.
As the presence of NOM generally had little impact (at pH values around 6) or enhanced oxidation of the four progestagenic compounds tested (at pH values around 8), reaction rates measured in Milli-Q water could therefore be used by operators as a conservative estimate to predict the oxidation of the four selected progestagens in natural source waters when exposed to permanganate. It could be presumed that under favorable conditions (alkaline pH and organic ligands) the oxidation can be enhanced relative to than predicted in pure water.
Effect of temperature on kinetic rate constants
Temperature effect on first-order apparent rate constants ( k , sec -1 ), oxidation rate constants ( k , M -1 sec -1 ) and activation energy (E a , KJ mol -1 ) for permanganate decay with and without progestagens (SH) in wastewater at pH 8.2 (WWTP A) a
Natural waters WWTP A (pH 8.2)
kKMnO4(×10–4 sec–1) without SH
184 ± 5
278 ± 9
302 ± 9
389 ± 13
20 ± 2
58 ± 1
115 ± 3
159 ± 4
171 ± 5
31 ± 2
1.9 ± 0.2
1.8 ± 0.8
4.4 ± 0.6
5.4 ± 0.2
172 ± 8
288 ± 12
368 ± 11
429 ± 13
26 ± 2
48 ± 1
89 ± 2
109 ± 3
112 ± 3
23 ± 7
Removal efficiencies and half-life
The elimination of SH by permanganate in Milli-Q and in wastewaters for pH 6.0 and pH 8.0, was investigated and values of removal percentage and half-life are summarized in Table 2.
Oxidation kinetics of four selected progestagens (progesterone, medroxyprogesterone, norethindrone and levonorgestrel) with permanganate were investigated as a function of pH, NOM and temperature. The second-order rate constants ranged for 23 to 224 M-1 sec-1 in Milli-Q water and 26 to 368 M-1 sec-1 in wastewater, at pH 6.0 and 8.0, respectively. It was found that a variation in pH did not significantly influence the rate constant. The impact of NOM at typical ranges found in wastewater effluents was also minimal with a slight enhancement of oxidation at pH values around 8. The removal of progestagens was lower for both progesterone and medroxyprogesterone than for levonorgestrel and norethindrone, i.e. 48 to 87% with half-lives between 2.1 and 44 min compared to 78 to 97% with half-lives between 2.7 and 5.6 min, in Milli-Q and wastewaters at pH 6.0-8.2, respectively.
This work demonstrates the potential of permanganate to oxidize progestagens in drinking water within the typical ranges of operational values of pH and NOM. Proper attention should be given to provide adequate CT values in order to ensure the efficient removal of progestagenic steroid hormones and recalcitrant analogues. Further kinetic studies targeting the identification and environmental impact of possible by-products related to progestagens reaction with permanganate appear warranted.
This work was made possible through the financial support from operating grants from the Natural Sciences and Engineering Research Council of Canada (NSERC), the Industrial Chair on Drinking Water at the École Polytechnique de Montréal and the Canadian Foundation for Innovation (equipment).
- Ternes TA, Joss A: Human Pharmaceuticals, Hormones and Fragrances. The Challenge of Micropollutants in Urban Water Management. 2007, London: IWA PublishingGoogle Scholar
- Kolpin DW, Furlong ET, Meyer MT, Thurman EM, Zaugg SD, Barber LB, Buxton HT: Pharmaceuticals, Hormones, and Other Organic Wastewater Contaminants in U.S. Streams, 1999−2000: A National Reconnaissance. Environ Sci Technol. 2002, 36: 1202-1211. 10.1021/es011055j.View ArticleGoogle Scholar
- Servos MR, Bennie DT, Burnison BK, Jurkovic A, McInnis R, Neheli T, Schnell A, Seto P, Smyth SA, Ternes TA: Distribution of estrogens, 17[beta]-estradiol and estrone, in Canadian municipal wastewater treatment plants. Sci Total Environ. 2005, 336: 155-170. 10.1016/j.scitotenv.2004.05.025.View ArticleGoogle Scholar
- Ying GG, Kookana RS, Ru YJ: Occurrence and fate of hormone steroids in the environment. Environ Int. 2002, 28: 545-551. 10.1016/S0160-4120(02)00075-2.View ArticleGoogle Scholar
- Purdom CE, Hardiman PA, Bye VVJ, Eno NC, Tyler CR, Sumpter JP: Estrogenic Effects of Effluents from Sewage Treatment Works. Chem Ecol. 1994, 8: 275-285. 10.1080/02757549408038554.View ArticleGoogle Scholar
- Routledge EJ, Sheahan D, Desbrow C, Brighty GC, Waldock M, Sumpter JP: Identification of Estrogenic Chemicals in STW Effluent. 2. In Vivo Responses in Trout and Roach. Environ Sci Technol. 1998, 32: 1559-1565. 10.1021/es970796a.View ArticleGoogle Scholar
- Desbrow C, Routledge EJ, Brighty GC, Sumpter JP, Waldock M: Identification of Estrogenic Chemicals in STW Effluent. 1. Chemical Fractionation and in Vitro Biological Screening. Environ Sci Technol. 1998, 32: 1549-1558. 10.1021/es9707973.View ArticleGoogle Scholar
- Lopez de Alda MJ, Diaz-Cruz S, Petrovic M, Barcelo D: Liquid chromatography−(tandem) mass spectrometry of selected emerging pollutants (steroid sex hormones, drugs and alkylphenolic surfactants) in the aquatic environment. J Chrom A. 2003, 1000: 503-526. 10.1016/S0021-9673(03)00509-0.View ArticleGoogle Scholar
- Auriol M, Filali-Meknassi Y, Tyagi RD, Adams CD, Surampalli RY: Endocrine disrupting compounds removal from wastewater, a new challenge. Process Biochem. 2006, 41: 525-539. 10.1016/j.procbio.2005.09.017.View ArticleGoogle Scholar
- Lopez de Alda MJ, Barcelo D: Review of analytical methods for the determination of estrogens and progestogens in waste waters. Fresenius J Anal Chem. 2001, 371: 437-447. 10.1007/s002160101027.View ArticleGoogle Scholar
- Briciu RD, Kot-Wasik A, Namiesnik J: Analytical Challenges and Recent Advances in the Determination of Estrogens in Water Environments. J Chrom Sci. 2009, 47: 127-139.View ArticleGoogle Scholar
- Viglino L, Aboulfadl K, Prevost M, Sauve S: Analysis of natural and synthetic estrogenic endocrine disruptors in environmental waters using online preconcentration coupled with LC-APPI-MS/MS. Talanta. 2008, 76: 1088-1096. 10.1016/j.talanta.2008.05.008.View ArticleGoogle Scholar
- Tomsikova H, Aufartova J, Solich P, Novakova L, Sosa-Ferrera Z, Santana-Rodriguez JJ: High-sensitivity analysis of female-steroid hormones in environmental samples. TrAC Trends Anal Chem. 2012, 34: 35-58.View ArticleGoogle Scholar
- Chang H, Wan Y, Wu S, Fan Z, Hu J: Occurrence of androgens and progestogens in wastewater treatment plants and receiving river waters: Comparison to estrogens. Water Res. 2011, 45: 732-740. 10.1016/j.watres.2010.08.046.View ArticleGoogle Scholar
- Sumpter JP, Johnson AC: Lessons from Endocrine Disruption and Their Application to Other Issues Concerning Trace Organics in the Aquatic Environment. Environ Sci Technol. 2005, 39: 4321-4332. 10.1021/es048504a.View ArticleGoogle Scholar
- Liu Z, Ogejo JA, Pruden A, Knowlton KF: Occurrence, fate and removal of synthetic oral contraceptives (SOCs) in the natural environment: A review. Sci Total Environ. 2011, 409: 5149-5161. 10.1016/j.scitotenv.2011.08.047.View ArticleGoogle Scholar
- Besse JP, Garric J: Progestagens for human use, exposure and hazard assessment for the aquatic environment. Environ Pollut. 2009, 157: 3485-3494. 10.1016/j.envpol.2009.06.012.View ArticleGoogle Scholar
- Kobayashi M, Sorensen P, Stacey N: Hormonal and pheromonal control of spawning behavior in the goldfish. Fish Physiol Biochem. 2002, 26: 71-84. 10.1023/A:1023375931734.View ArticleGoogle Scholar
- Kolodziej EP, Gray JL, Sedlak DL: Quantification of steroid hormones with pheromonal properties in municipal wastewater effluent. Environ Toxicol Chem. 2003, 22: 2622-2629. 10.1897/03-42.View ArticleGoogle Scholar
- Dinger JC, Heinemann LAJ, Kuhl-Habich D: The safety of a drospirenone-containing oral contraceptive: final results from the European Active Surveillance study on Oral Contraceptives based on 142,475 women-years of observation. Contraception. 2007, 75: 344-354. 10.1016/j.contraception.2006.12.019.View ArticleGoogle Scholar
- Runnalls TJ, Margiotta-Casaluci L, Kugathas S, Sumpter JP: Pharmaceuticals in the Aquatic Environment: Steroids and Anti-Steroids as High Priorities for Research. Hum Ecol Risk Assess. 2010, 16: 1318-1338. 10.1080/10807039.2010.526503.View ArticleGoogle Scholar
- Shore LS, Shemesh M: Naturally produced steroid hormones and their release into the environment. Pure Appl Chem. 2003, 75: 1859-1871. 10.1351/pac200375111859.View ArticleGoogle Scholar
- Koubovec D, Ronacher K, Stubsrud E, Louw A, Hapgood JP: Synthetic progestins used in HRT have different glucocorticoid agonist properties. Mol Cell Endocrinol. 2005, 242: 23-32. 10.1016/j.mce.2005.07.001.View ArticleGoogle Scholar
- Shao X, Ma J, Wen G, Yang J: Oxidationof estrone by permanganate: reaction kinetics and estrogenicity removal. Chin Sci Bull. 2010, 55: 802-808. 10.1007/s11434-010-0058-x.View ArticleGoogle Scholar
- Guan X, He D, Ma J, Chen G: Application of permanganate in the oxidation of micropollutants: a mini review. Front Environ Sci Engin China. 2010, 4: 405-413. 10.1007/s11783-010-0252-8.View ArticleGoogle Scholar
- Jiang J, Pang SY, Ma J, Liu H: Oxidation of Phenolic Endocrine Disrupting Chemicals by Potassium Permanganate in Synthetic and Real Waters. Environ Sci Technol. 2012, 46: 1774-1781. 10.1021/es2035587.View ArticleGoogle Scholar
- Hu L, Martin HM, Arce-Bulted O, Sugihara MN, Keating KA, Strathmann TJ: Oxidation of Carbamazepine by Mn(VII) and Fe(VI): Reaction Kinetics and Mechanism. Environ Sci Technol. 2008, 43: 509-515.View ArticleGoogle Scholar
- Hu L, Martin HM, Strathmann TJ: Oxidation kinetics of antibiotics during water treatment with potassium permanganate. Environ Sci Technol. 2010, 44: 6416-6422. 10.1021/es101331j.View ArticleGoogle Scholar
- Dash S, Patel S, Mishra BK: Oxidation by permanganate: synthetic and mechanistic aspects. Tetrahedron. 2009, 65: 707-739. 10.1016/j.tet.2008.10.038.View ArticleGoogle Scholar
- Rodriguez E, Majado ME, Meriluoto J, Acero JL: Oxidation of microcystins by permanganate: reaction kinetics and implications for water treatment. Water Res. 2007, 41: 102-110. 10.1016/j.watres.2006.10.004.View ArticleGoogle Scholar
- Ma J, Graham N: Controlling the formation of chloroform by permanganate preoxidation–Destruction of precursors. J Water Supply Res Technol -AQUA. 1996, 45: 308-315.Google Scholar
- Korshin GV, Chang HS, Frenkel AI, Ferguson JF: Structural Study of the Incorporation of Heavy Metals into Solid Phase Formed during the Oxidation of EDTA by Permanganate at High pH. Environ Sci Technol. 2007, 41: 2560-2565. 10.1021/es062554t.View ArticleGoogle Scholar
- Waldemer RH, Tratnyek PG: Kinetics of contaminant degradation by permanganate. Environ Sci Technol. 2006, 40: 1055-1061. 10.1021/es051330s.View ArticleGoogle Scholar
- Sharp EL, Parsons SA, Jefferson B: Seasonal variations in natural organic matter and its impact on coagulation in water treatment. Sci Total Environ. 2006, 363: 183-194. 10.1016/j.scitotenv.2005.05.032.View ArticleGoogle Scholar
- Sharp EL, Jarvis P, Parsons SA, Jefferson B: Impact of fractional character on the coagulation of NOM. Colloids Surf A Physicochem Eng Asp. 2006, 286: 104-111. 10.1016/j.colsurfa.2006.03.009.View ArticleGoogle Scholar
- Fabris R, Chow CWK, Drikas M, Eikebrokk B: Comparison of NOM character in selected Australian and Norwegian drinking waters. Water Res. 2008, 42: 4188-4196. 10.1016/j.watres.2008.06.023.View ArticleGoogle Scholar
- Forsberg C: Will an increased greenhouse impact in Fennoscandia give rise to more humic and coloured lakes?. Hydrobiologia. 1992, 229: 51-58. 10.1007/BF00006990.View ArticleGoogle Scholar
- Eikebrokk B, Vogt RD, Liltved H: NOM increase in Northern European source waters: Discussion of possible causes and impacts on coagulation/contact filtration processes. Water Sci Technol Water Supply. 2004, 4: 45-54.Google Scholar
- Worrall F, Burt TP: Trends in DOC concentration in Great Britain. J Hydrol. 2007, 346: 81-92. 10.1016/j.jhydrol.2007.08.021.View ArticleGoogle Scholar
- Worrall F, Burt TP: Changes in DOC treatability: Indications of compositional changes in DOC trends. J Hydrol. 2009, 366: 1-8. 10.1016/j.jhydrol.2008.11.044.View ArticleGoogle Scholar
- Matilainen A, Sillanpää M: Removal of natural organic matter from drinking water by advanced oxidation processes. Chemosphere. 2010, 80: 351-365. 10.1016/j.chemosphere.2010.04.067.View ArticleGoogle Scholar
- Pereira RO, Postigo C, de Alda ML, Daniel LA, Barcelo D: Removal of estrogens through water disinfection processes and formation of by-products. Chemosphere. 2011, 82: 789-799. 10.1016/j.chemosphere.2010.10.082.View ArticleGoogle Scholar
- Broseus R, Vincent S, Aboulfadl K, Daneshvar A, Sauve S, Barbeau B, Prevost M: Ozone oxidation of pharmaceuticals, endocrine disruptors and pesticides during drinking water treatment. Water Res. 2009, 43: 4707-4717. 10.1016/j.watres.2009.07.031.View ArticleGoogle Scholar
- Fayad PB, Prevost M, Sauve S: Laser Diode Thermal Desorption/Atmospheric Pressure Chemical Ionization Tandem Mass Spectrometry Analysis of Selected Steroid Hormones in Wastewater: Method Optimization and Application. Anal Chem. 2010, 82: 639-645. 10.1021/ac902074x.View ArticleGoogle Scholar
- AFNOR: Recueil de Normes Françaises; Qualité de l'Eau (French standards and regulations for the quality of water). 1994, Paris: Association Française de Normalisation, 403-Google Scholar
- Jiang J, Pang SY, Ma J: Role of Ligands in Permanganate Oxidation of Organics. Environ Sci Technol. 2010, 44: 4270-4275. 10.1021/es100038d.View ArticleGoogle Scholar
- Jiang J, Pang SY, Ma J: Oxidation of Triclosan by Permanganate (Mn(VII)): Importance of Ligands and In Situ Formed Manganese Oxides. Environ Sci Technol. 2009, 43: 8326-8331. 10.1021/es901663d.View ArticleGoogle Scholar
- Yan YE, Schwartz FW: Kinetics and Mechanisms for TCE Oxidation by Permanganate. Environ Sci Technol. 2000, 34: 2535-2541. 10.1021/es991279q.View ArticleGoogle Scholar
- Deborde M, Rabouan S, Gallard H, Legube B: Aqueous chlorination kinetics of some endocrine disruptors. Environ Sci Technol. 2004, 38: 5577-5583. 10.1021/es040006e.View ArticleGoogle Scholar
- Barbeau B, Desjardins R, Mysore C, Prevost M: Impacts of water quality on chlorine and chlorine dioxide efficacy in natural waters. Water Res. 2005, 39: 2024-2033. 10.1016/j.watres.2005.03.025.View ArticleGoogle Scholar
- Schulten HR: Models of Humic Structures: Association of Humic Acids and Organic Matter in Soils and Water. Humic Substances and Chemical Contaminants. Edited by: Clapp CE, Hayes MHB, Senesi N, Bloom PR, Jardine PM. 2001, Madison, WI: Soil Science Society of America, 73-87.Google Scholar
- He D, Guan X, Ma J, Yang X, Cui C: Influence of humic acids of different origins on oxidation of phenol and chlorophenols by permanganate. J Hazard Mater. 2010, 182: 681-688. 10.1016/j.jhazmat.2010.06.086.View ArticleGoogle Scholar
- Karanfil T, Kilduff JE, Schlautman MA, Weber WJ: Adsorption of Organic Macromolecules by Granular Activated Carbon. 1. Influence of Molecular Properties Under Anoxic Solution Conditions. Environ Sci Technol. 1996, 30: 2187-2194. 10.1021/es9505863.View ArticleGoogle Scholar
- Karanfil T, Schlautman MA, Kilduff JE, Weber WJ: Adsorption of Organic Macromolecules by Granular Activated Carbon. 2. Influence of Dissolved Oxygen. Environ Sci Technol. 1996, 30: 2195-2201. 10.1021/es950587v.View ArticleGoogle Scholar
- Chiou CT, Kile DE, Brinton TI, Malcolm RL, Leenheer JA, MacCarthy P: A comparison of water solubility enhancements of organic solutes by aquatic humic materials and commercial humic acids. Environ Sci Technol. 1987, 21: 1231-1234. 10.1021/es00165a012.View ArticleGoogle Scholar
- Chin YP, Weber WJ: Estimating the effects of dispersed organic polymers on the sorption of contaminants by natural solids. I. A predictive thermodynamic humic substance organic solute interaction model. Environ Sci Technol. 1989, 23: 978-984. 10.1021/es00066a008.View ArticleGoogle Scholar
- Ghosh K, Schnitzer M: Macromolecular structures of humic substances. Soil Sci. 1980, 126: 266-276.View ArticleGoogle Scholar
- Schlautman MA, Morgan JJ: Effects of aqueous chemistry on the binding of polycyclic aromatic hydrocarbons by dissolved humic materials. Environ Sci Technol. 1993, 27: 961-969. 10.1021/es00042a020.View ArticleGoogle Scholar
- Cameron RS, Thornton BK, Swift RS, Posner AM: Molecular weight and shape of humic acid from sedimentation and diffusion measurements on fractionated extracts. J Soil Sci. 1972, 23: 394-408. 10.1111/j.1365-2389.1972.tb01670.x.View ArticleGoogle Scholar
- Chen X, Xiao B, Liu J, Fang T, Xu X: Kinetics of the oxidation of MCRR by potassium permanganate. Toxicon. 2005, 45: 911-917. 10.1016/j.toxicon.2005.02.011.View ArticleGoogle Scholar
- Huang KC, Hoag GE, Chheda P, Woody BA, Dobbs GM: Kinetics and mechanism of oxidation of tetrachloroethylene with permanganate. Chemosphere. 2002, 46: 815-825. 10.1016/S0045-6535(01)00186-2.View ArticleGoogle Scholar
- Huang KC, Hoag GE, Chheda P, Woody BA, Dobbs GM: Oxidation of chlorinated ethenes by potassium permanganate: a kinetics study. J Hazard Mater. 2001, 87: 155-169. 10.1016/S0304-3894(01)00241-2.View ArticleGoogle Scholar
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