Next Article in Journal
Correlates of Unsupervised Bathing of Infants: A Cross-Sectional Study
Previous Article in Journal
Potential Changes in Rat Spermatogenesis and Sperm Parameters after Inhalation of Boswellia papyrifera and Boswellia carterii Incense

Int. J. Environ. Res. Public Health 2013, 10(3), 845-855; doi:10.3390/ijerph10030845

Article
Asellus aquaticus as a Potential Carrier of Escherichia coli and Other Coliform Bacteria into Drinking Water Distribution Systems
Sarah C. B. Christensen 1,*, Erik Arvin 1, Erling Nissen 2 and Hans-Jørgen Albrechtsen 1
1
DTU Environment, Technical University of Denmark, Bygningstorvet B115, 2800 Kgs. Lyngby, Denmark; E-Mails: erar@env.dtu.dk (E.A.); hana@env.dtu.dk (H.-J.A.)
2
VCS Denmark, Vandværksvej 7, 5000 Odense C., Denmark; E-Mail: en@vandcenter.dk
*
Author to whom correspondence should be addressed; E-Mail: scch@env.dtu.dk; Tel.: +45-452-51691; Fax: +45-459-32850.
Received: 9 January 2013; in revised form: 15 February 2013 / Accepted: 19 February 2013 /
Published: 1 March 2013

Abstract

: Individuals of the water louse, Asellus aquaticus, enter drinking water distribution systems in temperate parts of the world, where they establish breeding populations. We analysed populations of surface water A. aquaticus from two ponds for associated faecal indicator bacteria and assessed the risk of A. aquaticus transporting bacteria into distribution systems. Concentrations of up to two E. coli and five total coliforms·mL−1 were measured in the water and 200 E. coli and >240 total coliforms·mL−1 in the sediments of the investigated ponds. Concentrations of A. aquaticus associated bacteria never exceeded three E. coli and six total coliforms·A. aquaticus−1. During exposure to high concentrations of coliforms, concentrations reached 350 coliforms·A. aquaticus−1. A. aquaticus associated E. coli were only detected as long as E. coli were present in the water and sediment. The calculated probability of exceeding drinking water guideline values in non-disinfected systems by intrusion of A. aquaticus was low. Only in scenarios with narrow pipes and low flows, did total coliforms exceed guideline values, implying that the probability of detection by routine monitoring is also low. The study expands the knowledge base for evaluating incidents with presence of coliform indicators in drinking water by showing that intruding A. aquaticus were not important carriers of E. coli or other coliform bacteria even when emerging from faecally contaminated waters.
Keywords:
asellids; fresh water; indicator organisms; invertebrate; microbial; water louse

1. Introduction

The water louse Asellus aquaticus (Isopoda) is frequently found in drinking water distribution systems in temperate parts of the world (e.g., [1,2,3,4]). When A. aquaticus or other invertebrate animals enter a drinking water distribution system, they may be contaminated with bacteria, which can affect human health [5]. However, only few studies on this topic have been published and they mainly concern nematodes (e.g., [6,7]). The invertebrates may enter the systems via surface water, ground water or through leaks in clean water tanks and pipes created by bursts or maintenance work [2,8]. During repairs or maintenance work it is good practice to drain the hole around the pipe and exchange the pipe immediately. However, in practice incidences do occur for example during heavy rain events when surface water contaminates the pipe systems. Clean water tanks are often underground, which hinders observation of cracks in walls or ceilings from the outside and surface water animals may enter tanks through cracks, e.g., during heavy precipitations.

A. aquaticus from drinking water distribution systems have eyes and most specimens are coloured brown [1,9] in contrast to subsurface asellids (e.g., Proasellus cavaticus) which are transparent and have reduced or no eyes [9,10]. This indicates that even in water supplies based on groundwater, A. aquaticus most likely enter from surface water through deficiencies in the system. The public, press and water utilities in Denmark have shown an increasing interest in the occurrence of the animals in drinking water systems and raised concerns regarding drinking water safety.

Naturally occurring populations of A. aquaticus can survive at oxygen concentrations as low as 0.3 mg·L−1 and are known to thrive in highly eutrophic environments [11], where faecal bacteria are often present. However, A. aquaticus adapt to oligotrophic environments such as drinking water distribution systems, where they are able to form breeding populations and may survive even longer than in nature [1]. A. aquaticus is one of the largest invertebrates in drinking water systems. They are of particular interest as potential carriers of bacteria into drinking water systems when coming from contaminated environments, since the amount of bacteria associated with other investigated invertebrates (Hyalella azteca) depend on the size of the invertebrate [12]. Furthermore, A. aquaticus has been found to harbour bacteria from at least four different genera as symbionts in the digestive glands [13].

Escherichia coli and total coliform bacteria are widely used as indicators for faecal contaminations and as indicators of water quality in general [14,15] but some E. coli strains are also highly virulent (e.g., [16]). Other coliform bacteria can be present in both faeces and the environment (nutrient-rich waters, soil, decaying plant material) and some strains can even grow in drinking water distribution systems [17].

In water supply systems with distribution of drinking water without disinfection or disinfection residual such as in e.g., Denmark [1], the Netherlands [18] and Switzerland [19] there is no hygienic barrier against bacterial contaminations before the water reaches the end users. Therefore, bacteria transported into distribution systems by invertebrates may reach the consumers. In distribution systems with treatments such as chlorination or UV light, invertebrates may protect pathogens against the disinfection agents [12,20].

The aims of this study were to investigate whether A. aquaticus from surface waters are carriers of the faecal indicator organism E. coli or other coliform bacteria and if so, to estimate the probability of exceeding drinking water guideline values when A. aquaticus intrude drinking water distribution systems.

2. Materials and Methods

2.1. Sampling Locations

Two sampling locations near Kgs. Lyngby, Denmark were investigated. Pond 1 (55°47′17″ N, 12°31′30″ E) is an artificial eutrophic pond of 12 m2 approximately 0.3 meter deep with concrete sides and a sediment covered bottom. The vegetation was dominated by reeds, Nuphar sp. (waterlily) and Lemna minor (common duckweed) and the dominating non-aquatic fauna were waterfowl, mainly ducks. Pond 2 (55°46′57″ N, 12°33′47″ E) is situated in a deer park. It covers an area of 3,000 m2 and has a maximum depth of three to four meters, a muddy bottom and vegetation dominated by various reeds, Elodea canadensis (pondweed), Lemna trisulca (star duckweed) and Riccia fluitans (crystalwort). The dominating non-aquatic fauna were deer and waterfowl such as ducks and swans. Pond 2 is categorized as a Natura 2000 habitat 3150 “naturally eutrophic with floating vegetation”. With different fauna groups present in the two ponds, samples of coliform bacteria originated from birds as well as from mammals.

2.2. Sampling

Water, sediment and 60–100 A. aquaticus (depending on availability) were collected on each sampling occasion from pond 1 in January and October 2010 and from pond 2 in September and October 2010. Water was collected from the surfaces of the ponds 0.5 m from shore while sediment was sampled at 30 cm depth 0.5 m from shore. Water and surface sediment samples for analysis were taken by sterile pipettes and kept in two times five sterile 100 mL plastic containers while A. aquaticus were collected by a one mm meshed net and kept in three 500 mL glass containers containing water from the ponds. The average length was 10 mm but in the January samples, large hibernating specimens up to 25 mm were also sampled. All samples were transported to the lab within 15 min and analysed within 2 h. Two litres of pond water for the experiments with A. aquaticus were sampled on each sampling occasion in pre-combusted (550 °C for 18 h) blue cap bottles.

2.3. Analyses

Sediment, water and 10–20 A. aquaticus (depending on availability) from each sampling occasion were analysed for the presence of metabolically active E. coli and total metabolically active coliform bacteria by Colilert® (IDEXX Europe BV, Hoofddorp, The Netherlands) following the manufacturer’s instructions. Water and sediment samples were analysed in duplicates and triplicates. Ten mL wet sediment was extracted from the samples with sterile pipettes and dispersed in 90 mL autoclaved tap water before being poured into the Quanti-Tray®/2000 trays. One hundred mL of water was used for each analysis of the pond water. Quanti-Tray®/2000 trays were incubated at 37 ± 1 °C and after 20 ± 2 h the numbers of yellow wells were used to determine Most Probable Number (MPN) for total coliforms according to IDEXX Quanti-Tray®/2000 MPN Table provided by the manufacturer (IDEXX). The number of fluorescent wells under UV light was used to determine MPN for E. coli.

Prior to analysis, the animals were placed on absorbent tissue to remove attached water, grinded with a sterile pestle in a sterile tray and suspended in one mL autoclaved tap water. Two to four A. aquaticus were pooled for each Colilert® analysis. No distinction was made between adhering and internal bacteria, nor has this been studied in the available literature. Since detection by Colilert® relies on an enzymatic reaction, pre-experiments were carried out as described by Christensen et al. [21], establishing that grinded A. aquaticus did not influence the reaction. The pre-experiments also established that the absorbent tissue prevented bacteria from the water phase from being quantified together with the A. aquaticus associated bacteria. Because this study assessed the bacteria carried by A. aquaticus in vivo, the surfaces of A. aquaticus were not disinfected prior to analysis.

Total culturable heterotrophic bacteria, associated with A. aquaticus were measured as heterotrophic plate counts (HPC) on R2A agar (17209 Fluka Analytical, Sigma-Aldrich, Buchs, Switzerland) by plate spreading [22] with incubation at 20 ± 1 °C for 14 days.

2.4. Increased Concentrations of Coliform Bacteria

To study the association between A. aquaticus and coliform bacteria under increased concentrations of coliform bacteria, A. aquaticus from pond 2, September samples (which contained the highest concentrations of E. coli), were distributed in three sterile glass beakers (30 A. aquaticus in each). The beakers contained 450 mL pond water supplemented with 100 mL tap water (7 ± 1 °C) when 100 mL subsamples were taken, to maintain the volume, and were kept at 7 ± 1 °C for nine weeks. The temperature corresponded to temperatures in Danish distribution systems as well as the approximated average temperature of the ponds during sampling. Increased coliform growth rates would be expected under higher temperatures [23] however, the decay of E. coli under low temperatures is low [24]. Maple leaves which had been stored frozen and 50 mL drinking water sediment (wet volume), flushed from a fire hydrant, were added to the systems for A. aquaticus to feed on. Subsamples of the applied leaves and drinking water sediment were analysed by Colilert® and did not indicate presence of E. coli or other coliform bacteria.

2.5. Calculations

The concentration, C, of the bacteria released from A. aquaticus into the drinking water in a pipe was calculated by:

[C = M/Q]
where M is the source strength [# bacteria released·s−1] and Q is the flow rate (m3·s−1) in the pipe calculated by:
[Q = V × A]
where V = flow velocity (m·s−1) in pipe and A = flow area (m2) of the pipe.

The calculation gives a conservative assessment of the bacteria concentrations immediately after release to the water since it omits dispersion, sedimentation and inactivation which will reduce concentration over time.

3. Results and Discussion

3.1. A. aquaticus and Associated Coliform Bacteria from Surface Waters

A. aquaticus as well as E. coli and other coliform bacteria were present in the investigated ponds (Table 1). Only a maximum of three A. aquaticus associated E. coli and six A. aquaticus associated total coliforms were measured despite the relatively high concentrations of E. coli and total coliforms in water (two E. coli·mL−1 and five total coliforms·mL−1) and sediment (200 E. coli·mL−1 and >240 total coliforms·mL−1). No E. coli or other coliform bacteria were detected on large (25 mm long) hibernating A. aquaticus collected in January (Table 1).

Table Table 1. Concentrations of E. coli and total coliform bacteria in water, sediment and associated with A. aquaticus from two surface water ponds.

Click here to display table

Table 1. Concentrations of E. coli and total coliform bacteria in water, sediment and associated with A. aquaticus from two surface water ponds.
Pond 1Pond 2
January 2010 0 °C (ice cover)October 2010 11 °CSeptember 2010 5 °COctober 2010 6 °C
ETETETET
Water phase (MPN·mL−1)<0.010.030.01 ± 0.015 ± 1.92 ± 1.45 ± 1.90.1 ± 0.031 ± 0.05
Sediment phase (MPN·mL−1)<1<114 ± 9.7>240200 ± 6>240>86>170
Associated (MPN· A. aquaticus−1)<1<1<16 ± 43 ± 25 ± 21 ± 12 ± 1.5

E = E. coli, T = total coliform bacteria, total number of analysed A. aquaticus = 51, >indicates that the samples contain at least one measurement above the maximum measurable value.

The low degree of association between coliform bacteria and crustaceans was reported also from drinking water distribution systems. Levy et al. [5] observed that invertebrates collected from water distribution systems in Worcester, MA (USA) all harboured a variety of bacteria, however, no coliforms were associated with the invertebrates. Likewise, A. aquaticus have not been found to carry E. coli or other coliform bacteria in drinking water systems [1] and a sampling campaign of zooplankton and amoebae in drinking water did not reveal any associated E. coli or other coliform bacteria [25]. Other invertebrates show a higher degree of association with specific bacteria, e.g., copepod associated Vibrio sp. reached 7 × 104·copepod−1 [26] in spite of copepods being more than ten times smaller than asellids. More than 104 naturally occurring drinking water bacteria (HPCR2A agar 20 °C) per A. aquaticus have been measured in drinking water samples [21] and A. aquaticus host symbiotic bacteria in the hepatopancreases which is not the case for all crustaceans [13]. Hence A. aquaticus are able to host bacteria but were not important carriers of E. coli or other coliform bacteria though A. aquaticus were present in surface water environments with high concentrations of faecal contaminants.

3.2. A. aquaticus Associated Coliform Bacteria after Incubation

After incubation for nine weeks at 7 °C, the concentrations of total coliforms increased, while concentrations of E. coli decreased (Table 2). Accordingly, no E. coli were measured on the animals after nine weeks, while the number of total coliforms per A. aquaticus increased substantially, from five MPN per A. aquaticus from the pond to 350 MPN per A. aquaticus from the beakers. Numbers of A. aquaticus associated heterotrophic bacteria in the beakers were 1.3 × 105 CFU·A. aquaticus−1 (R2A, 20 °C) (Table 2), which is 400 times higher than the numbers of associated coliforms.

Table Table 2. Concentrations of bacteria from pond 2 in the beaker with the highest bacterial concentrations (September 2010, see Table 1) after nine weeks incubation. Total concentration in the beaker includes sediment and water concentrations.

Click here to display table

Table 2. Concentrations of bacteria from pond 2 in the beaker with the highest bacterial concentrations (September 2010, see Table 1) after nine weeks incubation. Total concentration in the beaker includes sediment and water concentrations.
E. coliTotal coliform bacteriaHPC (R2A, 20 °C)
Total conc. in beaker (MPN·mL−1)0.4>170NA
Water phase (MPN·mL−1)<0.0158NA
Sediment phase (MPN·mL−1)4>1,200NA
Associated (MPN or CFU· A. aquaticus−1)<13501.3 ± 0.09 × 105
Start sediment (MPN or CFU·mL−1)<1<13.3 ± 0.14 × 104

NA = not analysed, HPC = heterotrophic plate counts, total number of analysed A. aquaticus = 3, >indicates that the samples contain at least one measurement above the maximum measurable value. Start sediment is drinking water sediment before addition to the beakers.

Concentrations of heterotrophic bacteria in a non-chlorinated drinking water batch experiment, in which drinking water A. aquaticus was added, reached 1.8 × 104 CFU·A. aquaticus−1 (R2A, 20 °C). This was 700 times higher than the number of associated Klebsiella pneumoniae (MPN A. aquaticus−1), which was the coliform bacterium investigated in the study [21]. The only investigated A. aquaticus associated pathogen, Campylobacter jejuni, showed an even lower degree of association with A. aquaticus [21]. When expressed per mL A. aquaticus, HPC was also low (5.9 × 105 CFU·mL−1A. aquaticus) compared to microscopic crustaceans, on which bacterial numbers ranged between 9.7 × 107 and 5.6 × 108 CFU·mL−1 crustacean [27]. This indicates that other invertebrates may be more important carriers of bacteria than A. aquaticus.

3.3. Intrusion Scenarios

The loss of unaccounted for piped drinking water across the globe often amounts to more than 50% [28]. This number covers a large variability with e.g., the Netherlands and Denmark losing only 6–7% [29,30]. The loss occurs by spontaneous leakage in pipes, couplings, tanks, or during repair works as well as due to accidents during excavations. During these incidents the drinking water may be contaminated when the pressure in the pipes is zero or negative [31]. As a risk, normally unaccounted for, A. aquaticus is capable of moving against the flow and may enter the system even during positive pressure.

Two scenarios of intruding A. aquaticus are outlined. In the first, A. aquaticus enter a drinking water distribution system together with incoming contaminated water, which would occur during pressure loss in pipes or through cracks in clean water tanks during floodings. In the second scenario, single specimens of A. aquaticus enter the system e.g., by crawling against the flow in the water coming from a pipe leakage. The maximum concentrations of E. coli and total coliforms from the ponds (Table 1) and after nine weeks of incubation (Table 2) were used in the scenarios. According to the European Council Directive [15], E. coli and other coliform bacteria must be undetectable in 100 mL of drinking water. Both E. coli and total coliforms were regarded as water quality indicators in the following scenarios.

3.3.1. Scenario 1: Do A. aquaticus Contribute to the Transport of E. coli and Other Coliforms into Distribution Systems during Contaminations with Incoming Water and A. aquaticus Together?

In situations where A. aquaticus are transported into distribution systems together with contaminated water, and possibly also suspended sediment, e.g., during bursts or maintenance work, the water and sediment itself may transport coliform bacteria into the system. We assessed the contribution of E. coli and total coliforms from A. aquaticus compared to the contribution from incoming water and sediment. Total numbers of E. coli and total coliforms associated with one A. aquaticus equaled the numbers of bacteria in 1 mL incoming water (for E. coli) or 6 mL incoming water (for total coliforms) or 0.01 mL (for E. coli) or 0.3 mL (for total coliforms) in incoming sediment. Hence, the contaminated water and sediment itself can be considered a greater source of coliforms than the A. aquaticus transported with the water and sediment.

3.3.2. Scenario 2: Does Intrusion of Single A. aquaticus Specimens without Inflow of Water Cause Exceedings of Drinking Water Guideline Values for E. coli and Total Coliforms?

Normally, it is not considered as an option that bacteria can intrude against the water flow [31] but A. aquaticus is able to crawl into a pipe or tank against the flow when water is leaking out through deficiencies in pipes or vents [2], or even crawl short distances without water [10]. Hence, intrusion of A. aquaticus is possible without inflow of water. In Scenario 2, three intruding A. aquaticus are chosen for the calculations since more animals entering at the same time would most likely be due to a regular inflow of water containing animals, which is described in Scenario 1. In Scenario 2 we have used the maximum observed concentrations of associated bacteria in the ponds and after incubation (three E. coli and 350 total coliforms·A. aquaticus−1) (Table 1, Table 2). In a scenario with discharge of nine E. coli and 1,050 total coliform bacteria at once with a perfect mixing of the water, only one litre would contain water with E. coli concentrations >1/100 mL, while 110 L would contain water with total coliform concentrations >1/100 mL. This rough estimate provides an overview of the magnitude of the contamination, but is highly simplified and disregards that perfect mixing of the water does not take place in the pipes as well as a simultaneous discharge of all bacteria only occur in rare instances. To elaborate on the simple version of Scenario 2, the following parameters are considered:

(1)

All associated bacteria are not likely to be released from A. aquaticus instantly. Based on previous experiments we assume that they will be released over time, most likely days [12,21]. We have applied a variable, describing a uniform release over a time frame of one minute to seven days for total release of all coliform bacteria (Figure 1). However, due to dispersion, sedimentation and inactivation, not accounted for in this scenario, the approach is conservative and coliform concentrations are expected to be reduced further.

(2)

Pipe diameters of transmission and distribution pipes in most distribution systems vary by an order of magnitude (40–700 mm with an average of 150 mm in a large Danish distribution system). Pipes of 32–40 mm are typically connection pipes to private premises.

(3)

The flow rates in distribution systems vary according to the water demands and may even be stagnant e.g., during night. We have calculated the release of bacteria at two flow velocities (0.1 and 1 m·s−1).

The three variables influencing E. coli and total coliform concentrations in the water were defined as: (1) pipe diameter, (2) flow velocity of the water and (3) time for release of all bacteria.

Ijerph 10 00845 g001 1024
Figure 1. Illustration of E. coli and total coliform concentrations in the drinking water if three A. aquaticus enter a distribution system carrying the maximum observed concentrations (nine E. coli and 1,050 total coliforms). Horizontal lines show European Council Directive guideline values of E. coli and total coliforms in drinking water. The effects of the variables: pipe diameter, flow velocity and time for bacterial release, can be read in the illustration.

Click here to enlarge figure

Figure 1. Illustration of E. coli and total coliform concentrations in the drinking water if three A. aquaticus enter a distribution system carrying the maximum observed concentrations (nine E. coli and 1,050 total coliforms). Horizontal lines show European Council Directive guideline values of E. coli and total coliforms in drinking water. The effects of the variables: pipe diameter, flow velocity and time for bacterial release, can be read in the illustration.
Ijerph 10 00845 g001 1024

Drinking water guideline values for E. coli were not exceeded in any of the depicted scenarios (Figure 1). Nor did total coliform concentrations exceed guideline values in any scenarios with pipe diameters above 150 mm, but could surpass them in pipes with a diameter below 150 mm, when flow rates are low and all coliforms are released within a short period of time. This situation resemble incidents in which A. aquaticus intrude connection pipes where also the distance to the consumer is short and thereby also the time for decay of the bacteria. Unfortunately, many bursts occur in connection pipes, which call for special attention on working procedures concerning pipe work on connection pipes, where flushing through taps after repairs does not provide sufficiently high flow rates to flush out A. aquaticus [1]. However, even in these instances it is unlikely to detect A. aquaticus associated faecal indicator bacteria during routine monitoring of microbial drinking water quality due to the low sampling frequency.

4. Conclusions

A. aquaticus from surface water were demonstrated to carry high numbers of heterotrophic bacteria while the share of E. coli and other coliform bacteria was low. Conservative calculations showed that during contamination incidents, transport of E. coli and other coliform bacteria by A. aquaticus into drinking water distribution systems is not significant compared to transport by water and suspended sediment. Hence, intrusion of A. aquaticus is not likely to explain incidences of E. coli and total coliform exceeding guideline values in drinking water systems because the numbers of A. aquaticus associated coliform bacteria are insignificant. However, it still remains to be investigated whether A. aquaticus transport pathogens into drinking water systems in higher or lower numbers than the indicator organisms. The study expands the knowledge base for evaluating incidents with presence of coliform indicators in drinking water.

Acknowledgments

We greatly acknowledge VCS Denmark Ltd. and the UrbanWaterTech Graduate School for co-funding the project. Thanks to Lene Crafack, Camilla Lindgreen and Rune Jacobsen for providing data on hibernating A. aquaticus and to Lisbet Brusendorff for graphical work. Knud, Eigil and Alvin are acknowledged for their assistance in the field.

Conflict of Interest

The authors declare no conflict of interest.

References

  1. Christensen, S.C.B.; Nissen, E.; Arvin, E.; Albrechtsen, H.-J. Distribution of Asellus aquaticus and microinvertebrates in a non-chlorinated drinking water supply system—Effects of pipe material and sedimentation. Water Res. 2011, 45, 3215–3224. [Google Scholar]
  2. Van Lieverloo, J.H.M.; van der Kooij, D.; Hoogenboezem, W. Invertebrates and protozoans (free-living) in drinking water distribution systems. In Encyclopedia of Environmental Microbiology; Bitton, G., Ed.; Wiley: New York, NY, USA, 2002; pp. 1718–1733. [Google Scholar]
  3. Gauthier, V.; Gérard, B.; Portal, J.-M.; Block, J.-C.; Gatel, D. Organic matter as loose deposits in a drinking water distribution system. Water Res. 1999, 33, 1014–1026. [Google Scholar] [CrossRef]
  4. Walker, A.P. The microscopy of consumer complaints. J. Inst. Water Eng. Sci. 1983, 37, 200–214. [Google Scholar]
  5. Levy, R.V.; Hart, F.L.; Cheethan, R.D. Occurrence and public health significance of invertebrates in drinking water systems. Am. Water Works Assoc. J. 1986, 78, 105–110. [Google Scholar]
  6. Locas, A.; Barbeau, B.; Gauthier, V. 2007 Nematodes as a source of total coliforms in a distribution system. Can. J. Microbiol. 2007, 53, 580–585. [Google Scholar] [CrossRef]
  7. Lupi, E.; Ricci, V.; Burrini, D. Recovery of bacteria in nematodes isolated from a drinking water supply. J. Water SRT Aqua. 1995, 44, 212–218. [Google Scholar]
  8. Evins, C. Small animals in drinking water distribution systems. In Safe. Piped Water: Managing Microbial Water Quality in Piped Distribution Systems; Ainsworth, R., Ed.; World Health Organization, IWA Publishing: London, UK, 2004; pp. 101–120. [Google Scholar]
  9. Van Lieverloo, J.H.M.; van Buuren, R.; Veenendaal, G.; van der Kooij, D. How to Control Invertebrates in Distribution Systems: By Starvation or by Flushing? In Proceedings of the AWWA Water Quality Technology Conference, Denver, CO, USA, 9–12 November 1997.
  10. Holland, G.J. The eradication of Asellus aquaticus from water supply mains. J. Inst. Water Eng. 1956, 10, 220–241. [Google Scholar]
  11. Økland, K.A. Life history and growth of Asellus aquaticus (L.) in relation to environment in a eutrophic lake in Norway. Hydrobiologia 1978, 59, 243–259. [Google Scholar] [CrossRef]
  12. Levy, R.V.; Cheetham, R.D.; Davis, J.; Winer, G.; Hart, F.L. Novel method for studying the public health significance of macroinvertebrates occurring in potable water. Appl. Environ. Microbiol. 1984, 47, 889–894. [Google Scholar]
  13. Wang, Y.; Brune, A.; Zimmer, M. Bacterial symbionts in the hepatopancreas of isopods: Diversity and environmental transmission. FEMS Microbiol. Ecol. 2007, 61, 141–152. [Google Scholar] [CrossRef]
  14. Guidelines for Drinking-Water Quality; World Health Organization: Geneva, Switzerland, 2008.
  15. European Council Directive 98/83/EC of 3 November 1998 on the Quality of Water Intended for Human Consumption. Available online: http://www.iss.it/binary/publ/publi/0016.1109850012.pdf (accessed on 25 February 2013).
  16. Paton, J.C.; Paton, A.W. Pathogenesis and diagnosis of Shiga toxin-producing Escherichia coli infections. Clin. Microbiol. Rev. 1998, 11, 450–79. [Google Scholar]
  17. LeChevallier, M.W. Coliform regrowth in drinking water—A review. Am. Water Works Assoc. J. 1990, 82, 74–86. [Google Scholar]
  18. Van der Kooij, D. Potential for biofilm development in drinking water distribution systems. J. Appl. Microbiol. 1998, 85, 39–44. [Google Scholar] [CrossRef]
  19. Hammes, F.; Berger, C.; Koster, O.; Egli, T. Assessing biological stability of drinking water without disinfectant residuals in a full-scale water supply system. J. Water SRT Aqua. 2010, 59, 31–40. [Google Scholar] [CrossRef]
  20. Bichai, F.; Barbeau, B.; Payment, P. Protection against UV disinfection of E. coli bacteria and B. subtilis spores ingested by C. elegans nematodes. Water Res. 2009, 43, 3397–3406. [Google Scholar] [CrossRef]
  21. Christensen, S.C.B.; Nissen, E.; Arvin, E.; Albrechtsen, H.-J. Influence of Asellus. aquaticus on the indicator organisms Escherichia coli and Klebsiella. pneumoniae and the pathogen Campylobacter jejuni in drinking water. Water Res. 2012, 46, 5279–5286. [Google Scholar]
  22. Reasoner, D.J.; Geldreich, E.E. A new medium for the enumeration and subculture of bacteria from potable water. Appl. Env. Microbiol. 1985, 49, 1–7. [Google Scholar]
  23. Raghubeer, E.V.; Matches, J.R. Temperature range for growth of Escherichia coli stereotype O157, H7 and selected coliforms in E. coli medium. J. Clin. Microbiol. 1990, 28, 803–805. [Google Scholar]
  24. Flint, K.P. The long term survival of Escherichia coli in river water. J. Appl. Bacteriol. 1987, 63, 261–270. [Google Scholar] [CrossRef]
  25. Bichai, F.; Hijnen, W.; Baars, E.; Rosielle, M.; Dullemont, Y.; Barbeau, B. Preliminary study on the occurrence and risk arising from bacteria internalized in zooplankton in drinking water. Water Sci. Technol. 2011, 63, 108–14. [Google Scholar] [CrossRef]
  26. Heidelberg, J.F.; Heidelberg, K.B.; Colwell, R.R. Bacteria of the gamma-subclass Proteobacteria associated with zooplankton in Chesapeake Bay. Society 2002, 68, 5498–5507. [Google Scholar]
  27. Tang, K.W.; Turk, V.; Grossart, H.-P. Linkage between crustacean zooplankton and aquatic bacteria. Aqua. Microb. Ecol. 2010, 61, 261–277. [Google Scholar] [CrossRef]
  28. WHO and UNICEF. Global Water Supply and Sanitation Assessment 2000 Report. Available online: http://www.who.int/water_sanitation_health/monitoring/jmp2000.pdf (accessed on 25 February 2013).
  29. Vewin 2012. The Association of Dutch Water Companies. Available online: http://www.vewin.nl/english/Dutch%20water%20sector/Pages/default.aspx (accessed on 23 November 2012).
  30. DANVA’s Benchmarking and Water Statistics 2010. Available online: http://aoa.ew.eea.europa.eu/virtual-library-viewer/answer_8384288221 (accessed on 25 February 2013).
  31. Karim, M.R.; Abbaszadegan, M.; Le Chevallier, M. Potential for pathogen intrusion during pressure transients. Am. Water Works Assoc. J. 2003, 95, 134–146. [Google Scholar]
Int. J. Environ. Res. Public Health EISSN 1660-4601 Published by MDPI AG, Basel, Switzerland RSS E-Mail Table of Contents Alert