March 12, 2019
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Casanovas-Massana, A. and Blanch, A.R. 2019. E.coli and enterococci subtyping to discriminate contamination sources in wastewater treatment ponds. In: J.B. Rose and B. Jiménez-Cisneros, (eds) Global Water Pathogen Project. http://www.waterpathogens.org (S. Petterson and G. Medema (eds) Part 5 Case Studies) http://www.waterpathogens.org/book/e.coli-and-enterococci-subtyping-to-discriminate-contamination-sources-in-wastewater-treatment-ponds Michigan State University, E. Lansing, MI, UNESCO.
|Last published: March 12, 2019|
The objective of this case study was to determine whether the faecal contamination detected in two reclaimed open-air ponds used as a water reservoir for the irrigation of a golf course was related to a regrowth of the reclaimed water bacterial populations or to an input of faecal material related to the golf facility.
The golf facility was located in Catalonia (North-Eastern Spain), a region with an important affluence of national and international tourism, particularly in the summer. The summer season in this Mediterranean coastal region is generally dry and golf courses require irrigation to maintain the lawn surface quality. However, due to water scarcity in the summer period, the government encourages the use of reclaimed water for uses that do not require a drinking water quality. Thus, the construction of open-air ponds to temporally store reclaimed-water for later use is a common management practice in golf courses.
Figure 1. Location of the golf facility in North-Eastern Spain. The picture shows one of the open-air ponds in the golf course. (photo by A.R. Blanch)
The system studied consisted of two artificial outdoor storage ponds connected in series (pond A and pond B) used to irrigate a golf course. The volume of reclaimed water used for irrigation varied depending on the climatic conditions and the needs of the golf course in the different seasons. In the summer, irrigation was quite intensive, which resulted in a pond water residence time of around 2 weeks. In contrast, the pond water was barely used in the winter. These two ponds were filled with reclaimed water pumped from a local water reclamation plant. The reclamation process involved sand filtration followed by disinfection with a combination of chlorination and ultraviolet light.
This study showed that the source of the faecal pollution in the open-air ponds was not related to the reclaimed water, but to an input of faecal material occurring in the golf facility, most likely migrating birds. Physical barriers to reduce the faecal input from birds or additional in situ treatments may be necessary to reduce the contamination levels. Overall, this case-study shows that reclaimed water may be recontaminated after treatment in open-air reservoirs, and thus, the microbial quality should be monitored throughout its use.
In a global context of water scarcity the use of reclaimed water is expected to increase all around the world, and specifically in heavily populated coastal areas (Angelakis and Durham 2008). The use of reclaimed water may be a sound alternative for purposes that do not require a drinking water quality such as for crop irrigation, industrial activities, aquifer management, cleaning of streets, and ecological purposes among others. The irrigation of golf courses is one of the sectors where the use of reclaimed water is expected to increase due to government regulations aimed to reduce the use of primary water resources in drought periods. Reclaimed water is generally affordable, abundant and contains nutrients that may be beneficial for the maintenance of the golf course lawn (Mujeriego 2007).
Water reclamation technologies ensure high quality water effluents that fulfil the microbial regulations for golf course irrigation. However, several studies have reported the occurrence of microbial pathogens such as Cryptosporidium, Giardia, enteroviruses, enteropathogenic Escherichia coli, Legionella, Mycobacterium, Aeromonas, and Pseudomonas and the potential regrowth of some of these in reclaimed water distribution and storage systems (Costán-Longares et al. 2008; Gennaccaro et al. 2003; Jjemba et al. 2010; Ryu et al. 2005). In addition, the recontamination of stored reclaimed water by faecal pathogens from wildlife or domestic animals (Nemec and Massengale 2010; Vogel et al. 2007), urban runoff (Sauer et al. 2011), or septic system failure (Ahmed et al. 2005a) cannot be ruled out, particularly when water is open-air stored. This case study explores the origin of the low levels of faecal pollution detected in two reclaimed water open-air ponds used as a reservoir for the irrigation of a golf course in North-eastern Spain.
The purpose of this study was to determine whether the low levels of faecal contamination detected in two reclaimed water ponds used as a reservoir for the irrigation of a golf facility located in Catalonia (North-Eastern Spain) was related to a regrowth of the microbial populations introduced with the reclaimed water or to an input of faecal material occurring in the golf facility during storage.
The system consisted of two artificial outdoor ponds connected in series (pond A and pond B) which were used as reservoirs for the irrigation of a golf course. The capacity of pond A was 21,000 m3 and that of pond B was 13,000 m3. The volume of reclaimed water used for irrigation varied depending on the climatic conditions and the needs of the golf course in the different seasons. In summer, irrigation was quite intensive, which resulted in a pond water residence time of around 2 weeks. In contrast, the pond water was barely used in winter. These two ponds were yearlong filled with reclaimed water pumped from a nearby water reclamation plant. The reclamation process involved sand filtration followed by disinfection with a combination of chlorination and ultraviolet light. These treatments ensured that the concentration of E. coli remained below 200 CFU/100 mL, which is the limit established for water reclamation in Spain (Anonymous, 2007). The historical series obtained from the laboratory of the reclamation plant confirmed that at the end of the treatment the concentrations of E. coli were 20 CFU/100 mL as a 90th percentile of the annual dataset.
To determine whether the microbial faecal populations in the ponds were similar to those from the treated wastewater, we collected six water samples at three points in the system: the inflow of the reclamation plant, pond A, and pond B. Three of the samples were taken in the summer and another three in the winter. We enumerated faecal coliforms and faecal enterococci by filtering and incubating in selective culture media (mFC agar for faecal coliforms and m-Enterococcus agar followed by confirmation in Bile Esculin agar for faecal enterococci). Then, we randomly selected 25 well-isolated colonies for each sample and bacterial indicator and performed a biochemical phenotyping using the PhP-RE and PhP-RF plates of the Phene-Plate System™ (Bactus AB. Based on the biochemical profiles obtained for each sample, we calculated Simpson's diversity index (Di) and the similarity index (Sp), a similarity coefficient that measures the proportion of isolates that are identical in two compared samples (Kühn 1985; Kühn et al. 1991; Hunter and Gaston 1988). Then, the similarity coefficients were clustered using UPGMA and the populations of both faecal indicators at the three sampling points were compared to a database of populations associated with slaughterhouse wastewater (faecal contamination of animal origin) or human sewage available from previous studies (Blanch et al. 2003; Kühn et al. 2005; Manero et al. 2006; Vilanova et al. 2004). In total, the database consisted of 3,556 faecal coliform isolates and 1,127 enterococci.
In addition, we studied the inactivation of faecal coliforms (FC), total bifidobacteria (TBIF), sorbitol-fermenting bifidobacteria (SBIF), somatic bacteriophages (SOM), and bacteriophages infecting Bacteroides thetaiotaomicron (BACT) in ponds to determine whether they could regrow during storage in the ponds. A water sample from pond B was spiked with a 1:50 dilution of sewage water from the treatment plant. This matrix was used to fill dialysis tubes with a porosity cutoff of 14 kDa (Medicell Dialysis Tubing Visking, London, UK). The dialysis tubes with 50 mL of the water dilution were placed at a depth of 20–25 cm from the surface of pond B. Dialysis tubes were retrieved from the system at different incubation times for a period of 2 weeks in the winter and 1 week in the summer. Independent assays were performed three times during the summer and four times during the winter to enumerate all the microbial indicators. The enumeration results were used to calculate the inactivation kinetics of the culturable populations. The following equations were used to calculate the decay rates (Ks) and the time required for 90 % of the initial population to decay (T90 values (in hour)):
where Nt is the cell concentration per milliliter at time t, and N0 is the initial cell concentration per milliliter (at time t0).
The concentrations of faecal coliforms in the reclaimed water did not significantly vary between winter and summer, and were always low (1.25 log10 CFU/ 100 mL) fulfilling the standards established by Spanish regulations for golf course irrigation (Anonymous 2007). In the winter, the ponds also presented very low numbers of faecal coliforms and enterococci (<0.10 log10 CFU/100 mL), even lower than those in the reclaimed water. In contrast, in summer, the numbers were higher than in winter or in the reclaimed water with average concentrations around 2.75 log10 CFU/100 mL (Table 2). This indicated that the microbial quality of the water deteriorated during storage in the ponds in the summer season.
A total of 308 enterococci (225 in summer and 83 in winter) and 315 faecal coliforms (225 in summer and 90 in winter) were isolated and biochemically phenotyped. We observed high diversity values for both populations in the secondary-treated sewage in summer and in winter (Di > 0.94) in line with previous studies (Blanch et al. 2003; Vilanova et al. 2004). The diversity index was more moderate in the ponds in the summer and was especially low for the enterococci in pond A. In general, low FIB diversities have been related to inputs of faecal pollution associated with few individuals (Kühn et al. 1997). In winter, the diversity indices in the ponds could not be compared to those in summer because of the low number of enterococci and faecal coliforms isolated.
The analysis of the similarity coefficients in summer indicated that faecal coliforms and faecal enterococci populations in pond A and pond B were highly similar (Sp > 0.2), which indicated that they shared the same biochemical profile structure. This result strongly pointed out to a shared source of faecal pollution for both ponds. On the other hand, the populations of faecal coliforms and enterococci in the secondary-treated sewage were different from those isolated in ponds A and B (Sp < 0.2). In contrast, we found no similarity between the faecal coliforms or enterococci populations of the secondary-treated sewage, pond A and pond B in the winter. However, the small number of isolates obtained in this season, reduced the strength of these coefficients.
Finally, the faecal coliform/enterococci ratio (FC/E) was low in the summer, which suggested that the source of the faecal pollution was animal related as it has been previously observed that low FC/E ratios are often related to faecal contamination of animal origin (Feachem 1975; Geldreich and Kenner 1969). Although the validity of this ratio has been questioned (Jagals and Grabow 1996; Sinton et al. 1998), it may serve as a preliminary indicator. The reclamation plant processed exclusively human sewage and presented higher FC/E ratios making it an unlikely source of the pollution in the ponds.
None of the faecal microbial indicators studied was able to regrow or even persist in the ponds for an extended time. On the contrary, they all presented clear inactivation kinetics, which were significantly different between the microorganisms (p < 0.0086 in summer and p < 0.0032 in winter). The inactivation rate of the faecal microbial indicators followed the sequence: SBIF > TBIF > FC > BACT > SOM both in summer and in winter, with the lowest and highest T90 for bifidobacteria and somatic coliphages, respectively. These results are consistent with results reported previously (Chung and Sobsey 1993; Durán et al. 2002; Moce-Llivina et al. 2005; Sinton et al. 1999), in which SOM and BACT were more persistent than faecal coliforms and other indicators in sewage, seawater, and freshwater. Additionally, the low persistence of bifidobacteria confirmed the results previously obtained for river water (Bonjoch et al. 2009). Overall, these results provide evidence that the faecal microbial indicators that entered the ponds through the reclaimed water could not regrow in the natural environment, and consequently, the reclaimed water could not be the source of the increased levels of FIB in the ponds.
Overall, our data suggest that there was a source of faecal matter in the ponds other than the reclaimed water. Indeed, large numbers of birds, particularly Anas platyrhynchos and Anser anser, were observed in and around the ponds in summer. In winter, these birds were hardly ever seen. This suggests that the high pollution levels detected in summer might be related to their droppings. Therefore, although the reclaimed water complied with sanitary regulations, the microbial quality of the water deteriorated during the residence time in the ponds, probably due to wildlife activity. From a general point of view, these results point out an important limitation in the current reclaimed water regulation, which does not foresee the potential recontamination of properly disinfected waters and its consequences (Anonymous 2007). As a result, the legal interpretation of recontamination is complex, and therefore, its health implications should be studied to gain a better understanding of the associated risks. Nevertheless, our results suggest that a disinfection treatment achieving concentrations of E. coli around 1 log unit at the 90th percentile ensures that ponds will not exceed the regulatory limit of 200 CFU/100 mL considering the in situ input of faecal matter from diffuse pollution, birds or other wildlife.
The authors thank the Consorci de la Costa Brava for its help with the sampling and Dr. Javier Méndez from the University of Barcelona for his help with the statistical analysis. This study was supported by the Xarxa de Referència en Biotecnologia. Arnau Casanovas-Massana was supported by a grant from the Spanish Ministry of Education. This case study was derived from a research project, the results of which are published in the following journal article:
Casanovas-Massana, A., and Blanch, A.R. (2013) Determination of faecal contamination origin in reclaimed water open-air ponds using biochemical fingerprinting of enterococci and faecal coliforms. Environmental Science and Pollution Research. 20:3003-3010. doi:10.1007/s11356-012-1197-1.
The biological hazards presented by faecal contamination in stored reclaimed water were assessed using the enumeration of faecal coliforms and enterococci in several sampling points along the year. Inactivation of faecal microbial indicators in the ponds was analysed on-site. Biochemical fingerprinting of both bacterial indicator populations was performed to determine the faecal source (human or non-human) based on reference biochemical profiles associated to faecal sources. The use of this approach was chosen because the concentration of E.coli when detected in storage ponds was below the detection limit of most of Microbial Source Tracking molecular techniques (<0.10 log10 CFU/100 mL in winter, and 2.7 log10 CFU/100 mL in summer). A total of 308 enterococci and 315 faecal coliforms were isolated and biochemically phenotyped using the PhP-RF and PhP-RE plates.