versão On-line ISSN 1816-7950
versão impressa ISSN 0378-4738
Water SA vol.40 no.1 Pretoria Jan. 2014
Tero LuukkonenI; Juhani TeeriniemiI; Hanna ProkkolaI; Jaakko RämöII; Ulla LassiI, III
IUniversity of Oulu, Department of Chemistry, FI-90014, University of Oulu, Finland
IIUniversity of Oulu, Thule institute, FI-90014 University of Oulu, Finland
IIIKokkola University Consortium Chydenius, Unit of Applied Chemistry, Talonpojankatu 2B, FI-67100 Kokkola, Finland
Peracetic acid (PAA) has been studied for wastewater disinfection applications for some 30 years and has been shown to be an effective disinfectant against many indicator microbes, including bacteria, viruses, and protozoa. One of the key advantages compared to, e.g., chlorine is the lack of harmful disinfection by-products. In this paper a pilot-scale study of PAA-based disinfection is presented. Indicator microbes (E. coli, total coliforms and coliphage viruses) as well as chemical parameters (pH, oxidation-reduction potential (ORP), chemical and biochemical oxygen demand (COD and BOD), and residual PAA and hydrogen peroxide) were studied. The main aim of this investigation was to study how these selected chemical parameters change during PAA treatment. Based on the results, disinfection was efficient at C-t values of 15 to 30 (mg-min)/ℓ which equals to a PAA dose of 1.5 to 2 mg/ℓ and a contact time of 10 to 15 min. In this concentration area changes in pH, COD and BOD were negligible. However, hydrogen peroxide residues may interfere with COD measurements and apparent COD can be higher than the calculated theoretical oxygen demand (ThOD). Additionally PAA or hydrogen peroxide residues interfere with the BOD test resulting in BOD values that are too low. Residual PAA and ORP were found to correlate with remaining amounts of bacteria.
Keywords: tertiary wastewater disinfection, peracetic acid, total coliform, E. coli, coliphages
Wastewater treatment has traditionally focused on the removal of solids, organic material and nutrients (phosphorus and more recently nitrogen). Additionally, microbes in wastewater are typically removed up to about 98% in a conventional treatment process without disinfection (Tchobanoglous et al., 2004). Remaining pathogens are often thought to diminish via dilution in natural waters or to be inactivated by stress factors such as pH, temperature, salinity, nutrient availability, and oxidative stress (Rozen and Belkin, 2001). However, this is not always sufficient if there are activities taking place which involve the receiving water body, such as bathing, fishing or fish farming for example. Globally, microbiological quality of wastewater is becoming ever more important due to the water scarcity in many areas and therefore the need to recycle or reuse treated wastewater is now considerably higher than before.
There are many alternative techniques for wastewater disinfection that can be used individually or in combination: chlorine compounds (gas and hypochlorite), chlorine dioxide, ultraviolet (UV) radiation, ozone, and peracetic acid (PAA). Chlorine is still globally the most common disinfectant due to its low cost, however the awareness of harmful by-products and the formation of chlorination-resistant bacteria strains causes wastewater plants to consider other options. Recently performic acid (PFA) has also been proposed as a wastewater disinfectant but additional research is necessary as there are currently no published results about, e.g., by-product formation and toxicity effects (Gehr et al., 2009).
The role of PAA in wastewater disinfection has been extensively studied since the early 1980s and PAA has also been used as a disinfectant for many years in the food, beverage, and paper industries (Orth, 1998; Rasimus et al., 2011). PAA is commercially available as a stabilised equilibrium mixture containing PAA (typically 5 to 15% w/w), hydrogen peroxide, acetic acid, and water (Eq. (1)). PAA is considered to be the main active component in the solution (Baldry, 1983; Baldry and French, 1989; Fraser et al., 1985; Kitis, 2004; Lubello et al., 2002).
The disinfection efficiency of PAA in wastewater applications has been demonstrated numerous times in the literature (Antonelli et al., 2006; Baldry, 1983; Baldry and French, 1989; Baldry et al., 1991; Baldry et al., 1995; Briancesco et al., 2005; Collivignarelli et al., 2000; Dell'Erba et al., 2004; Gehr et al., 2003; Kitis, 2004; Koivunen and Heinonen-Tanski, 2005a; Koivunen and Heinonen-Tanski, 2005b; Lefevre et al., 1992; Liberti and Notarnicola, 1999; Liberti et al., 1999; Salgot et al., 2002; Veschetti et al., 2003; Zanetti et al., 2007). As a result, PAA is gaining acceptance as a disinfectant, especially in the United Kingdom and Italy (Falsanisi et al., 2006). Examples of full-scale installations include Milan Nosedo wastewater treatment plant (WWTP) in Italy and Mikkeli Kenkävero WWTP in Finland.
A recent study by Azzellino et al. (2011) showed that PAA disinfection is more dependent on dosage than on contact time. This indicates that the traditional C.t (dose amount x contact time) concept may need a weighting coefficient for the t term. Additionally, PAA seems to possess faster inactivation kinetics for E. coli compared to total coliform bacteria (TCB), which was also confirmed by Mezzanotte et al. (2007). These findings are important in terms of selecting a representative indicator microbe and interpreting disinfection test results.
Although PAA has been shown to be relatively insensitive towards suspended solids (Koivunen and Heinonen-Tanski, 2005b; Lefevre et al., 1992) or organic materials (Koivunen and Heinonen-Tanski, 2005b), in wastewater it seems reasonable to apply PAA disinfection to effluents that are as well-processed as possible. General effects of wastewater chemical and physical characteristics on disinfection with PAA are shown in Table 1. The best results can be expected when treating filtered tertiary effluents, i.e., applying the so-called multiple barrier concept (Liberti and Notarnicola, 1999). Large and heavy parasites (e.g. helminth eggs) are removed by filtration and smaller pathogens such as viruses and bacteria are destroyed by disinfection. However, De Velásquez et al. (2008) showed recently that PAA, per se, is effective against helminth eggs, although relatively high doses are needed.
Additional hygienic safety can be achieved by combining UV and PAA, which can be classified as an advanced oxidation process (AOP) (Lubello et al., 2002; Koivunen and Heinonen-Tanski, 2005a; Caretti and Lubello, 2003; Rajala-Mustonen et al., 1997). This UV/PAA synergy is based on an enhanced formation of radicals (e.g., hydroxyl radicals, OH•), which makes the conditions very unfavourable to microbes as the two techniques complement each other (Bianchini et al., 2002). Another way to improve disinfection efficiency is the addition of copper or silver ions with PAA (De Velásquez et al., 2008; Luna-Pabello et al., 2009).
Disinfection by-product (DBP) formation during PAA disinfection has been studied by Dell'Erba et al. (2007), who found that no brominated or chlorinated phenols are formed. While some formation of aldehydes did occur, PAA tends to further oxidise them to carboxylic acids and eventually to carbon dioxide. They also stressed that the amount of formed aldehydes never exceeded the Italian maximum allowable concentrations. Another study was performed by Crebelli et al. (2005) who used bacterial mutagenicity and plant genotoxicity tests to assess the formation of harmful DBPs. Their results using 2 to 4 mg/ℓ of PAA and a contact time of 26 to 37 min in secondary settled effluent suggested that no formation of genotoxic DBPs took place. Similar results were also obtained by Monarca et al. (2002).
In this paper PAA was used to disinfect tertiary municipal wastewater effluent within a pilot scale set-up. The following chemical parameters were monitored before and after the disinfection process: chemical oxygen demand (CODCr), biochemical oxygen demand (BOD7,ATU), pH, oxidation-reduction potential (ORP) and, finally, residual PAA and hydrogen peroxide concentrations. Disinfection efficiency was assessed by monitoring the following indicator microorganisms: coliform bacteria (E. coli and total) and coliphage viruses (F-specific and somatic). The purpose of this study was to clarify how selected chemical parameters change during PAA disinfection.
Disinfection tests were performed at Oulu WWTP in Taskila, Finland. The pilot plant consisted of a circular contact basin in which tertiary effluent from the full-scale WWTP was fed by using a submersible pump (Fig. 1). Mixing of the PAA chemical and wastewater was performed by a set-up involving an overflow weir. Contact time in the basin was adjustable by controlling the inlet valve and was tested using food dye. PAA was added to the water entering the contact basin with the aid of a diaphragm pump.
Characteristics of tertiary effluent before disinfection
The process employed at Taskila's WWTP process consists of pre-treatment (screening and aerated sand separation), primary treatment (polyaluminium chloride dosing, mixing, seasonal flocculating polymer dosing, and sedimentation), secondary treatment (activated sludge process with denitrification and nitrification stages, ferric sulphate and seasonal flocculating polymer dosing, and sedimentation), and tertiary treatment (sand filtration). Tertiary sand filters are used for the removal of solids and denitrification whilst methanol feeding to sand filters is used as an additional carbon source. The main characteristics of the tertiary effluent are shown in Table 2.
Chemicals and methods
ORP (oxidation reduction potential) and pH were measured with a multiparameter probe (Ezodo 7300) in situ at the pilot plant. The ORP probe consisted of a platinum test electrode together with a reference Ag/AgCl electrode.
Chemical oxygen demand (CODCr) was measured with a Hach Lange DR 2800 photometer using Hach Lange cuvette tests which employed the closed reflux dichromate method. Biochemical oxygen demand with allylthiourea (ATU) addition and a measurement time of 7 days (BOD7,atu) was determined using the OxiTop manometric respirometric method under OECD 301F standard conditions.
Residual PAA and hydrogen peroxide concentrations were measured using a Chemetrics V2000 photometer and cuvette tests (K-7913 for PAA and modified K-5543 for H2O2). The K-5543 cuvette test method for H2O2 measurements was modified by adding 5 drops of approximately 11% potassium iodide solution (Chemetrics) to each sample before testing to remove the possible interference caused by PAA.
Samples used for E. coli, TCB, and coliphage virus analysis were collected in sterile PET bottles. Sodium thiosulphate solution (FF-chemicals) was then added to the samples to quench the residual PAA (9 g/ℓ solution with 1 µℓ to 1 mℓ sample dosing). TCB and E. coli were analysed according to the Finnish standard method SFS 3016:2001 whilst coliphage viruses were analysed according to EPA Method 1602 using a dual or single layer agar technique. Hosts used were E. coli CN-13 (ATCC#700609) and E. coli Famp (ATCC#700891), for somatic and F specific coliphages, respectively. Coliphage virus analyses were performed at the National Institute for Health and Welfare of Finland.
Finally, the PAA chemical used in the study was PACS12 (Solvay) which contained 12% (w/w) PAA, 20% hydrogen peroxide and 20% acetic acid.
RESULTS AND DISCUSSION
Effect of PAA doses on the ORP and pH
The results of ORP measurements at different PAA doses are shown in Fig. 2. For comparison, changes in ORP in primary settled effluent are also shown. The initial ORP of tertiary effluent (an average of about 150 mV) indicates a generally oxidative situation and the presence of free oxygen (Goncharuk et al., 2010). ORP changes quite steeply in the concentration area of 0.1 to 1.0 mg/ℓ PAA whereas higher levels of PAA concentration only result in a slight increase in the ORP. A similar trend also applies to primary effluent. An increase in ORP is in part related to the decomposition of PAA and hydrogen peroxide and subsequent release of dissolved oxygen. At higher doses, the effluent quickly becomes saturated with oxygen and therefore the rate of increase in ORP settles down.
There are numerous publications available about the applications of ORP in water and wastewater disinfection, especially with chlorination (Kim and Hensley, 1997; Bergendahl and Stevens, 2005; Yu and Cheng, 2003). Bergendahl and Stevens (2005) showed that when ORP is greater than 650 mV, it ensures bacterial inactivation against E. coli, Salmonella or Pseudomonas, which is in agreement with WHO guidelines for keeping ORP at 700 mV during the disinfection of drinking water (Goncharuk et al., 2010). In addition, Kim and Hensley (1997) showed that ORP correlates better than chlorine residual with residual coliform bacteria. We conducted a similar test with PAA and our results (Fig. 3) showed that a linear correlation between residual PAA and TCB or E. coli values is slightly better (correlation coefficients being -0.975 and -0.934, respectively) than for ORP and total coliform amounts (correlation coefficients being -0.948 and -0.829, respectively). Both ORP and residual PAA can be monitored online for modulating the chemical feed. As with chlorine-based disinfection (Kim and Hensley, 1997), these parameters can be used for the optimisation of chemical consumption. However, it may be necessary to determine the correlation of bacterial amounts and ORP in each WWTP site individually.
Changes in pH were plotted against dosed PAA (mg/ℓ) resulting in a linear fit with R2 = 0.854:
As municipal wastewaters are generally well buffered against pH changes by bicarbonates, only relatively small decreases in pH take place per each added mg/ℓ of PAA. Koivunen and Heinonen-Tanski (2005b) reported that 7 mg/ℓ of PAA dose decreased the pH by 0.24 and 0.18 pH units in secondary and tertiary wastewater, respectively. These numbers are consistent with our results.
Chemical and biochemical oxygen demand
Changes in BOD7,atu, CODCr, and theoretical oxygen demand (ThOD) at different PAA concentrations are shown in Fig. 4. ThOD was calculated by assuming that all PAA reacts to acetic acid and then is oxidised completely according to Eq. (3).
Changes in ThOD depend on the composition of the used PAA chemical (i.e. the ratio of PAA to conjugate acetic acid). In this particular case the addition of 1 mg/ℓ of PAA increases COD about 4.0 mg/ℓ O2. For comparison, Kitis (2004) calculated a 2.8 mg/ℓ O2 increase in COD for the addition of 1 mg/ℓ of PAA.
COD follows the ThOD curve quite closely; however, there are several measurements showing signiicantly higher COD values than ThOD. This is possibly due to the interference caused by residual hydrogen peroxide (Talinli and Anderson, 1992). Several possible reactions have been reported in literature (Eqs. 4-7) explaining how hydrogen peroxide could react with the standard oxidising agent, the dichromate ion (Cr2O72-) (Talinli and Anderson, 1992). One such possible complex structure is shown in Fig. 5 (Grampp et al., 2002).
Reactions 4-7 can cause a positive error in the COD results. Talinli and Anderson (1992) pointed out that even water samples containing no organic compounds had COD values if they contained hydrogen peroxide. This topic was further studied by Kang et al. (1999) who proposed an empirical correction equation for the interference. Lee et al. (2011) discovered that 1 mg of H2O2 caused an increase of 0.50 to 0.58 mg of COD in anaerobically digested livestock wastewater. In a recent study, Wu and Englehardt (2012) proposed a chemical method for the removal of hydrogen peroxide interference. Their method employs addition of sodium carbonate and heating.
To the best of the authors' knowledge, the interference of hydrogen peroxide in the COD measurement has not been represented earlier in the context of PAA-based wastewater disinfection. This could be one of the reasons for the statement (e.g. Lazarova et al. (1998)) that PAA treatment substantially increases the organic load of the treated wastewater. However this is not the case if PAA is used in moderate doses.
Changes in BOD are well below those in ThOD and there seems to even be a slight decrease in BOD (BOD change being negative) in the concentration area of 1 to 2 mg/£ PAA. Interestingly Baldry et al. (1995) reported that the mean COD, as well as BOD, fell during the full-scale trial with PAA. In that case, the PAA dose was 5 mg/ℓ with a contact time of 10 min. Their trial was performed at a WWTP which receives textile industry wastes in addition to domestic wastewater. A decrease in the mean COD and BOD could possibly be attributed to the oxidation of organics in the textile wastewater. For comparison, Fig. 6 shows data collected from Mikkeli Kenkävero WWTP in Finland which is using PAA disinfection for their final effluent. The data shows for the same period of time in consecutive years 2010 (no PAA disinfection) and 2011 (PAA disinfection in use) an average increase of 2.8 mg/ℓ O2 for BOD7ATU. Some of this increase may be natural variation in the effluent quality.
Figure 7 shows changes of BOD during the measurement of BOD7,ATU for tertiary effluent containing 0 to 5 mg/ℓ PAA. The method used (OxiTop) measures the change of gas pressure as biodegradation produced CO2 is absorbed by NaOH pellets. The initial negative BOD readings can be interpreted as a release of oxygen and subsequent increase of pressure. However after about 23 to 47 h this effect diminishes, depending on the PAA dose. It is also possible that PAA residual functions as a biocide and causes inhibition of biodegradation in the first 47 h.
However, it seems that biodegradation starts very quickly after residuals are consumed after 47 h.
Residual peracetic acid and hydrogen peroxide
PAA-based wastewater disinfection usually leaves small residues of PAA and H2O2 in the effluent, as stated by, e.g., Veschetti et al. (2003). Typically, decomposition of PAA occurs in 2 phases: (i) initial, almost instantaneous decrease in concentration and (ii) subsequent slow decomposition of residual (Antonelli et al., 2006; Falsanisi et al., 2006). It is difficult to discriminate between factors affecting the initial decrease: e.g. particulates, reduced organic species, iron, manganese and micro-organisms have been shown to have effects (Falsanisi et al., 2006). Small amounts of PAA and hydrogen peroxide are, however, considered harmless to an aquatic environment and have been suggested to be beneficial in reducing the amounts of biofilms in effluent discharge pipes (Koivunen and Heinonen-Tanski., 2005b). Small residues of H2O2 are constantly present in water bodies as H2O2 is generated in the surface water layers by sunlight - initiated through photoredox reactions involving organic compounds (e.g. humic or fulvic acids), dissolved oxygen and trace metals (e.g. Fe or Mn) (Stumm and Morgan, 1996; Scully et al., 1995).
Results of PAA and H2O2 residual measurements after 1 min of contact time are presented in Fig. 8. Dashed lines represent zero consumption.
Amounts of male-specific (F+) and somatic coliphage viruses present in pre-treated (screening and sand removal) and tertiary effluents, together with disinfection results, are presented in Table 3. The process employed at the Taskila WWTP appeared to remove a substantial proportion of coliphage viruses, even without disinfection, during our test period (comparing pre-treated and tertiary effluent). Residual viruses are effectively removed with a dose of 1 mg/ℓ PAA and a contact time of 60 min. However, there is a variation in disinfection results as dose is increased. This could be due to changes in the amount of coliphage viruses in the water to be disinfected.
Rajala-Mustonen et al. (1997) also studied the removal of coliphage virus with PAA but their doses were substantially higher. Mattle et al. (2011) reported that MS2 bacteriophage (an F-specific coliphage) was not inactivated by PAA in the absence of chloride.
The amounts of TCB and E. coli on a logarithmic scale as a function of C*t are shown in Fig. 9. The dashed lines in Fig. 9 illustrate the Finnish bathing water standards for inland and seashore areas (Ministry of Social Affairs and Health Decree 177/2008) which sets the quality requirements for monitoring of public bathing waters. Values below this standard indicate excellent bathing water quality. In terms of E. coli this means < 250 CFU/100 mℓ (coastal area) or < 500 CFU/100 mℓ (inland). In our experiments, these standards were achieved with a value of approx. 15 to 30 (mg-min)/ℓ which equals to a dose of 1.5 to 2 mg/ℓ PAA and a contact time of 10 to 15 min. In Finland there are no general requirements to disinfect wastewater effluents prior to discharge. However, if there are, e.g., bathing or recreational activities in the receiving water body, disinfection is demanded by the WWTP's individual environmental licence. As discharge waters are diluted in the receiving water body the required microbial quality is typically in the order of 2 000 CFU/100 mℓ for E. coli.
Our results demonstrate the effectiveness of PAA as a disinfectant using common indicator microbes E. coli, total coliforms and coliphage viruses. A dose of 1.5 to 2 mg/ℓ with a contact time of 10 to 15 min appears to be sufficient for bacteria removal from tertiary effluent and similar doses with a contact time of about 60 min for coliphage virus removal. However, there was variation in virus disinfection results at larger PAA doses.
We measured the following chemical parameters before and after PAA disinfection: pH, ORP, CODCr , BOD7ATU, and residual PAA and H2O2. There were negligible changes in the pH (about 0.5 pH units), even at about 15 mg/ℓ of PAA, whilst ORP increased steeply within the concentration area of 0.1 to 1 mg/ℓ. At concentrations greater than 1 mg/ℓ PAA the rate of increase diminishes. This is possibly due to a saturation of dissolved oxygen produced by the PAA and H2O2 decomposition. ORP was observed to correlate with residual bacterial amounts in the same way as reported in existing literature for chlorine-based disinfection. However, the correlation between residual bacterial amounts and residual PAA was found to be slightly better. CODCr followed ThOD values closely but some measurements showed substantially larger COD than ThOD. This is due to the interference caused by hydrogen peroxide which is well documented in the literature. Finally, as residues of PAA may inhibit bacteria from decomposing organic material, BOD7,atu measurements may be inaccurate.
This study was partially funded by the Finnish Funding Agency for Technology and Innovation (TEKES) and PAC-Solution Ltd. The authors greatly appreciate these bodies' financial support. The authors would like to thank the whole staff of PAC-Solution Ltd and Oulun Vesi waterworks for valuable comments and co-operation during the study. The authors acknowledge the participation of Satu Hukkanen, Ville Kaikkonen, Lauri Parviainen, and Hanna Runtti for their assistance in conducting the tests and taking samples.
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+35 844 535-3695
Received 4 February 2013
accepted in revised form 6 December 2013