Hydrogeology Journal

, Volume 25, Issue 4, pp 931–938

Future research needs involving pathogens in groundwater

Paper

Abstract

Contamination of groundwater by enteric pathogens has commonly been associated with disease outbreaks. Proper management and treatment of pathogen sources are important prerequisites for preventing groundwater contamination. However, non-point sources of pathogen contamination are frequently difficult to identify, and existing approaches for pathogen detection are costly and only provide semi-quantitative information. Microbial indicators that are readily quantified often do not correlate with the presence of pathogens. Pathogens of emerging concern and increasing detections of antibiotic resistance among bacterial pathogens in groundwater are topics of growing concern. Adequate removal of pathogens during soil passage is therefore critical for safe groundwater extraction. Processes that enhance pathogen transport (e.g., high velocity zones and preferential flow) and diminish pathogen removal (e.g., reversible retention and enhanced survival) are of special concern because they increase the risk of groundwater contamination, but are still incompletely understood. Improved theory and modeling tools are needed to analyze experimental data, test hypotheses, understand coupled processes and controlling mechanisms, predict spatial and/or temporal variability in model parameters and uncertainty in pathogen concentrations, assess risk, and develop mitigation and best management approaches to protect groundwater.

Keywords

Microbial processes Contamination Groundwater monitoring Health Groundwater/surface-water relations 

Besoins en recherche pour le futur impliquant les agents pathogènes dans les eaux souterraines

Résumé

La contamination des eaux souterraines par des agents pathogènes entériques a souvent été associée à l’apparition de maladies. Une gestion adéquate et un traitement des sources des agents pathogènes sont des prérequis importants pour prévenir d’une contamination des eaux souterraines. Cependant, les sources diffuses de contaminations pathogènes sont fréquemment difficiles à identifier, et des approches existantes pour la détection des agents pathogènes sont coûteuses et ne fournissement que seulement des informations semi-quantitative. Des indicateurs microbiens qui sont facilement quantifiables souvent ne sont pas corrélés avec la présence d’agents pathogènes. Les agents pathogènes constituant une nouvelle préoccupation et l’augmentation des détections de la résistance aux antibiotiques parmi les pathogènes bactériens dans les eaux souterraines sont des sujets de préoccupation croissante. Une élimination adéquate des agents pathogènes pendant le passage dans le sol est donc essentielle pour une exploitation de eaux souterraines en toute sécurité. Les processus susceptibles de favoriser le transport d’agents pathogènes (par exemple, des zones de vitesse élevée et d’écoulements préférentiels) et de diminuer l’élimination des agents pathogènes (par exemple, la rétention réversible et une survie accrue) sont particulièrement préoccupants, car ils augmentent le risque de contamination des eaux souterraines, mais sont encore mal compris. L’amélioration de la théorie et des outils de modélisation sont nécessaires pour analyser des données expérimentales, tester des hypothèses, comprendre les processus couplés et les mécanismes de contrôle, prédire la variabilité spatiale et/ou temporelle des paramètres des modèles et de l’incertitude des concentrations en agents pathogènes, évaluer le risque, et développer des mesures d’atténuation et de meilleures méthodes de gestion pour protéger les eaux souterraines.

Necesidades futuras de investigación relacionadas con patógenos en el agua subterránea

Resumen

La contaminación del agua subterránea por patógenos entéricos se ha asociado comúnmente con brotes de enfermedades. La gestión y el tratamiento adecuados de las fuentes de patógenos son requisitos previos importantes para prevenir la contaminación del agua subterránea. Sin embargo, las fuentes no puntuales de contaminación de patógenos son a menudo difíciles de identificar, y los enfoques existentes para su detección son costosos y sólo proporcionan información semicuantitativa. Los indicadores microbianos que se cuantifican fácilmente a menudo no se correlacionan con la presencia de patógenos. Los patógenos de preocupación emergente y la creciente detección de la resistencia a los antibióticos entre los patógenos bacterianos en el agua subterránea son temas de creciente preocupación. La eliminación adecuada de patógenos durante el pasaje en el suelo es por lo tanto crítica en la extracción segura del agua subterránea. Los procesos que aumentan el transporte de patógenos (por ejemplo, zonas de alta velocidad y flujo preferencial) y disminuyen la eliminación de patógenos (por ejemplo, retención reversible y supervivencia mejorada) son de especial preocupación porque aumentan el riesgo de contaminación del agua subterránea, pero todavía no son comprendidos. Se necesitan herramientas mejoradas de la teoría y modelado para analizar los datos experimentales, probar hipótesis, entender los procesos acoplados y los mecanismos de control, predecir la variabilidad espacial y/o temporal de los parámetros del modelo y la incertidumbre en las concentraciones de los patógenos, la evaluación de riesgos y el desarrollo de la mitigación y una mejor gestión de los enfoques para proteger el agua subterránea.

未来的研究需要涉及地下水中的病原体

摘要

肠道病原体造成的地下水污染通常与疾病爆发有关。病原体源的恰当管理和处理是预防地下水污染的重要先决条件。然而,病原体非点源污染常常难以确定,现有的病原体检测方法费用昂贵,并且仅仅提供半定量信息。容易量化的微生物指标常常与病原体的存在没有对应关系。新兴的对病原体的关注及地下水中细菌性病原体抗生素抗性的越来越多的检测成为越来越受到关注的主题。因此,病原体在土壤通道中被充分除去对于安全的地下水开采至关重要。增强病原体运移的过程(例如高速带和优先流)及减少消除病原体的过程(例如可逆滞留及增强的存活时间)受到特别关注,因为这些过程增加了地下水污染的风险,然而,这些过程仍然没有被完全了解。需要改进的理论和模拟工具来分析实验数据,检验假设,了解耦合过程和控制机理,预测模型参数中空间和/或时间上的变化及病原体含量的不确定,评价风险性以及开发缓解和最佳管理方法,以保护地下水。

Futuras necessidades da pesquisa envolvendo patógenos em águas subterrâneas

Resumo

A contaminação das águas subterrâneas por patógenos entéricos tem sido frequentemente associada a surtos de doença. A gestão e o tratamento adequados de fontes de patógenos são requisitos importantes na prevenção da contaminação das águas subterrâneas. No entanto, as origens não pontuais de contaminação por patógenos são frequentemente difíceis de identificar e as abordagens existentes para a detecção de patógenos são dispendiosas e somente fornecem informação semi-quantitativa. Os indicadores microbianos que são facilmente quantificados, com frequência não se correlacionam com a presença de patógenos. São tópicos de inquietação crescente os problemáticos patógenos emergentes e a crescente detecção de patógenos bacterianos com resistência antibiótica em águas subterrâneas. A adequada remoção de patógenos durante a passagem pelos solos é consequentemente crítica para a extração de água subterrânea segura. Os processos que favorecem o transporte de patógenos (p.e., zonas de alta velocidade ou de fluxo preferencial) e os que atenuam a remoção de patógenos (p.e., retenção reversível e aumento de sobrevivência) são dignos de preocupação especial porque aumentam o risco de contaminação das águas subterrâneas, mas ainda estão incompletamente compreendidos. São necessárias novas ferramentas teóricas e de modelagem para analisar os dados experimentais, testar hipóteses, compreender processos acoplados e mecanismos de controle, predizer a variabilidade espacial e/ou temporal nos parâmetros do modelo e a incerteza nas concentrações de patógenos, avaliar o risco e desenvolver abordagens de mitigação e de gestão otimizada para a proteção das águas subterrâneas.

Introduction

Groundwater constitutes ∼95% of the world’s usable reserve of fresh liquid water, supplies about half the drinking water in the United States (Maupin and Barber 2005), 75% of the drinking water in Europe, and is the principal source of drinking water for as many as 2 billion people worldwide (Alley 2006). Although traditionally considered less vulnerable to contamination by pathogens than surface water, groundwater is responsible for a disproportionate fraction of reported waterborne disease outbreaks (Jin and Flury 2002). Contributions of groundwater to the global burden of waterborne disease outbreaks are difficult to estimate accurately due to a lack of reliable data; however, where systematic, long-term data were collected regarding the sources of such outbreaks, it appears that pathogen-contaminated groundwater is often a major cause—for example, statistics collected from 1998 to 2012 for a national outbreak surveillance system in Scandinavia indicate that most of the waterborne disease outbreaks having a known water source (76%) were linked to groundwater (Guzman-Herrador et al. 2015). Waterborne disease outbreak surveillance data collected in the US over a 36-year period (1971–2006) indicate that a majority (52%) of the deficiencies associated with drinking-water disease outbreaks involved either untreated or inadequately treated groundwater, compared with 19% for untreated or inadequately treated surface water (Craun et al. 2010). Although there was a marked decrease in outbreak risks associated with surface water in public systems during this period, there was no corresponding decrease in outbreak risks associated with untreated or inadequately treated groundwater (Craun 2012).

Groundwater-related outbreak statistics in the US relate, at least in part, to the observation that approximately one in six households obtain drinking water from private wells for which there is little regulation (Rogan and Brady 2009; Wallender et al. 2014). In a pooled analysis of groundwater systems in the US and Canada (1990–2013), 15% (216 of 2,210) of groundwater samples tested positive for enteric pathogens (Hynds et al. 2014). More than 150 enteric viruses can contaminate groundwater (Wong et al. 2012) as can many pathogenic bacteria including Arcobacter butzleri, Campylobacter spp., Escherichia coli, Helicobacter pylori, Legionella spp., Salmonella spp., Shigella spp., Vibrio cholera, and Yersinia spp., and pathogenic protists such as Cryptosporidium spp., Encephalitozoon intestinalis, Giardia lamblia, and Naegleria fowleri (Tufenkji and Emelko 2011). Table 1 provides a summary of recent waterborne disease outbreaks with known etiology that were caused by consumption of contaminated groundwater. In addition to quantification of the occurrences of pathogens in well water, more comprehensive epidemiological studies will be needed in the future to quantify groundwater-related health risks (Murphy et al. 2014).
Table 1

Selected recent waterborne disease outbreaks with known etiology that were caused by consumption of contaminated groundwater

Pathogen(s)

Location

Year

Cases

Deaths/hospital

Reference

Viruses

 Norovirus genogroup 1 and 2

Jeju Island,S. Korea

2004

194

NR

Kim et al. 2005

 Norovirus genogroup 1.2

S. Korea

2011

4,451

NR

Cho et al. 2014

 Norovirus genogroup 1.2

Sicily, Italy

2011

156

NR

Giammanco et al. 2014

 Norovirus

New Mexico, USA

2011

119

0/0

Beer et al. 2015

 Norovirus genogroup 1.2

Wisconsin, USA

2012

19

0

Beer et al. 2015

 Norovirus genogroup 1.2

Wisconsin, USA

2007

229

0/6

Borchardt et al. 2011

 Norovirus

Wyoming, USA

2001

230

NR

Blackburn et al. 2004

Bacteria

Campylobacter jejuni, & Yersinia enterocolitica

Alaska, USA

2001

12

NR

Blackburn et al. 2004

Campylobacter sp.

Roros, Norway

2007

105

0/7

Jakopanec et al. 2008

E. coli O157:H7 & Campylobacter jejuni

Walkerton, Canada

2000

2,300

7/160

Howard 2006

E. coli O157:H7 & O121

Arizona, USA

2011

56

0/2

Beer et al. 2015

Legionella pneumophila

Washington, USA

2011

3

1/3

Beer et al. 2015

L. pneumophila

Ohio, USA

2011

11

1/11

Beer et al. 2015

L. pneumophila

Pennsylvania, USA

2011

6

1/5

Beer et al. 2015

L. pneumophila

Pennsylvania, USA

2012

2

1/2

Beer et al. 2015

L. pneumophila

Maryland, USA

2011

7

1/6

Beer et al. 2015

Protozoa

Cryptosporidium sp.

Indiana, USA

2001

10

NR

Blackburn et al. 2004

G. intestinalis

Utah, USA

2012

28

0/0

Beer et al. 2015

G. intestinalis

Florida, USA

2001

6

NR

Blackburn et al. 2004

N. fowleri

Arizona, USA

2002

2

2/2

Gerba et al. 2009

Multiple types

Campylobacter coli, Norovirus, & Rotavirus group A

Gourdon, France

2000

202

0/6

Gallay et al. 2006

Giardia sp., Salmonella typhimurium, & Norovirus

Ohio, USA

2004

1,540

NR/21

Fong et al. 2007

The transport and fate of pathogens from dispersed fecal sources through the heterogeneous subsurface to groundwater wells depend on a wide variety of incompletely characterized physical, chemical, and microbiological factors, and considerable knowledge gaps exist (Bradford et al. 2013). Because pathogens impair more than 2 million ha of lakes and over 480,000 km of shoreline in the US alone (US EPA 2010a), more research is clearly needed concerning the roles of surface-water–groundwater exchanges in pathogen transmission to wells. Furthermore, there is concern that the risk of pathogen contamination to groundwater may increase in the future because of ever-increasing demand for potable groundwater; extreme weather events associated with climate change, land use alterations, and ecological disturbances; waterborne diseases of emerging concern; and the proliferation of managed aquifer recharge and on-land waste disposal. Consequently, more directed studies will be needed to meet future challenges regarding the safety of groundwater sources.

The purpose of this paper is to identify and discuss some of the more critical knowledge gaps and potential directions for future studies involving the transport and fate of pathogens in groundwater. This paper is not meant as a comprehensive review. Factors that influence the transport and fate of pathogens in soils and aquifers cover a vast body of published literature and the interested reader is referred to more detailed information in the following reviews: Schijven and Hassanizadeh 2000; Ginn et al. 2002; Jin and Flury 2002; Bradford et al. 2013, 2014; Molnar et al. 2015.

Selected critical issues needing additional research

Microbial pathogens such as viruses, bacteria, and protozoan parasites are found in the fecal wastes excreted by humans, domesticated animals, wildlife, and insects (Gerba and Smith 2005). Contamination of groundwater can originate from point or non-point sources. Although well-defined point sources can facilitate the study of field-scale pathogen fate and transport, highly variable non-point sources can be major sources of groundwater contamination (Sobsey et al. 2001). Additional research is needed to identify, treat, and manage pathogen sources of groundwater contamination. This management includes better on-land disposal practices regarding domestic wastewater, agriculture practices, and storm-water runoff. For the latter topic, optimized design of engineered infiltration systems could substantially reduce the pathogen and indicator loading from urban areas.

Quantitative determination of pathogen concentrations in complex environmental samples such as groundwater is costly and time consuming. Pathogen abundances in environmental samples are often below the detection limit using current methods, so large volumes of water frequently need to be filtered before analysis (Toze 1999; Sobsey et al. 2001; Lazcka et al. 2007). The recovery efficiency of pathogens from filters and environmental samples is often low and variable (Sobsey et al. 2001), and it may therefore be a critical limiting step in determining quantitative pathogen concentrations that has received limited research attention. Typical methods used to assess pathogen concentrations (fluorescent stains, fluorescence in situ hybridization, monitoring of specific activity, or molecular approaches such as qPCR that amplify selective gene sequences in extracted nucleic acids) require specialized equipment and personnel, and frequently only produce semi-quantitative concentrations for a single pathogen (Toze 1999; Sobsey et al. 2001). Consequently, more research is needed to measure in a cost-effective and timely manner the abundances of pathogens in groundwater environments. New, more sensitive and (or) efficient methods of pathogen detection are needed to more accurately determine the distribution of pathogens in groundwater used as sources of drinking water. Techniques such as solid-state cytometry (Stevenson et al. 2014), comprehensive droplet digital detections (Kang et al. 2014), and advanced molecular methods (Ramírez-Castillo et al. 2015) may facilitate future studies by providing more accurate and timely information.

Due to the high costs and extreme difficulties in accurately determining pathogen concentrations, regulations to protect public health from pathogens (US EPA 2006, 2010b) only require the periodic monitoring for easily measured indicator microorganisms such as total or fecal coliform (FC), Enterococcus, and E. coli. However, recent studies indicate that current indicators such as coliform bacteria often do not correlate well with pathogens of interest. For example, in a study involving contaminated groundwater in Bangladesh, it was found that culture-dependent indicators of fecal contamination failed to predict total bacterial pathogens (Ferguson et al. 2012). Furthermore, little research attention has been paid to differences in the source, transport, and fate of indicators and pathogens, although pronounced differences are expected. Bacillus subtilis spores were recently found to serve as a conservative surrogate for the transport, retention, and release of Cryptosporidium parvum oocysts (Headd and Bradford 2016; Bradford et al. 2016). Further investigations are needed to select indicators that are representative of other pathogen sources, transport, and fate.

Emerging infectious diseases, most of which are caused by zoonotic pathogens, constitute a major threat to public health (Daszak et al. 2007). Groundwater contamination caused by “emerging pathogens” or “pathogens of emerging concern” will continue to be an important research topic in the future. Increasing detections in groundwater of emerging bacterial pathogens such as H. pylori (Ryan et al. 2014), only recently linked to ulcers and gastrointestinal cancers, and Arcobacter, which has been linked to a number of gastrointestinal diseases (Hsu and Lee 2015), suggest additional research is needed on this topic. In particular, more and better data from the field will be needed in order to develop required inputs for a quantitative microbial risk assessment in order to establish guidelines that would safeguard human health while considering sources of uncertainty (Ryan et al. 2014).

The public health challenges presented by pathogens in groundwater are exacerbated by recent increases in reported instances of antibiotic resistance (Böckelmann et al. 2009; Economides et al. 2012; Bech et al. 2014), which make waterborne diseases harder to treat. Indeed, antibiotic resistance in the environment has been identified as one of the more important infectious disease issues in the United States (Ashbolt et al. 2013), with intensive use of antibiotics in agricultural activity (Bech et al. 2014) and overprescribing of antibiotics (Binder et al. 1999) being major contributors to this problem. The report that 23 of the 25 V. cholerae O1 strains isolated from stream and well water samples in Cameroon exhibited multiple antibiotic resistance (Akoachere et al. 2013) underscores the seriousness of antibiotic resistant bacteria (ARB) in groundwater. Future studies need to account for selective pressures that facilitate ARB, identify and quantify the rates of horizontal gene transfer in ARB propagation, and modify outdated dose–response methodologies for application to ARB (Ashbolt et al. 2013).

The ultimate distance that pathogens can be transported in porous media depends on survival and reversibility of retention; however, the retention rate is typically much higher than the decay (death/inactivation) rate. Hence, retention is viewed as the major contribution to protection of drinking-water aquifers from pathogen contamination; furthermore, porous medium surfaces potentially could be designed to remove pathogens near the source or downgradient at the wellhead. Numerous studies of pathogen retention and release, particularly at the interface-, pore-, and column-scales, have demonstrated extreme sensitive to a multitude of physical, chemical, and microbiological factors. At the field-scale, many of these properties are subject to large spatial and temporal variability that collectively hamper accurate quantification of retention and release parameters and their distribution in situ. Consequently, there is a critical need to be able to predict more accurately the influence of physicochemical factors on pathogen retention and release in the subsurface. Factors that affect retention, enhanced release, and diminish retention capacity (e.g., transients in ionic strength, pH, solution composition, temperature, and colloids and solutes that compete for the same retention sites as pathogens) are of special interests and deserve more research attention because they can increase the risk of pathogen transport. Also important are factors that lead to non-exponential declines in retention with transport distance such as straining, surface, size, or morphologic heterogeneity within a microbial population, variability in hydrodynamic conditions, and blocking.

A number of theoretical approaches have been developed to quantify pathogen retention and release in the subsurface under various physicochemical conditions. Filtration theory considers that the retention rate depends on the mass transfer and immobilization of pathogens on the solid surface. A number of correlation equations have been developed to predict the mass transfer of microbes to the solid-water interface (SWI) under highly idealized pore geometries. New research is needed to study microbe mass transfer to the SWI under conditions that are more representative of natural pore space geometries with wide ranges in grain size distributions, grain-grain contact characteristics, and pore-throat diameters and geometries.

Pathogen immobilization and release from the SWI depends on Brownian, adhesive, and hydrodynamic forces and/or torques that collectively act on the nearly neutrally buoyant microbe. Additional research is warranted to quantify more accurately these forces and torques, especially the influence of pathogen shape, roughness, chemical heterogeneity, and short-range (e.g., nm-scale) interactions in adhesive forces. Computer simulations that have explicitly accounted for these forces and torques indicate that nanoscale chemical and roughness heterogeneity control immobilization at low velocity and high ionic strength, especially for smaller microbes (Pazmino et al. 2014; Bradford and Torkzaban 2015). Conversely, surface straining (entrapment) at microscopic roughness locations and grain-grain contacts has been found to control immobilization under low ionic strength and high velocity conditions, especially for larger microbes, by substantially increasing and decreasing the lever arms associated with adhesive and hydrodynamic torques, respectively. These findings are generally consistent with micromodel observations of colloid and microbe retention in porous media, and observed differences of retention in batch and column studies (Treumann et al. 2014; Torkzaban and Bradford 2016). Simulation results also indicate that nanoscale heterogeneity creates spatial variability in depths of interaction energy (primary or secondary) minima on the SWI that can induce short- or long-term immobilization at a particular location. These observations demonstrate the complexity of boundary conditions for pathogen immobilization at the SWI, and challenge filtration theory assumptions of a constant sticking efficiency and transport at a constant average pore-water velocity. Additional research is needed to resolve better these issues at the interface- and pore-scales, and to upscale simulation results to physically meaningful continuum-scale parameters under steady-state and transient physicochemical conditions.

Rates of microbial retention are generally greater than those of decay (death and inactivation), although there are some notable exceptions (Schijven and Hassanizadeh 2000). It is often difficult to quantify separately the processes of liquid-phase decay and irreversible retention; also, solid-phase decay can hamper accurate determination of reversible retention. Improved experimental procedures are needed to separately quantify decay and retention processes and obtain mass balance, especially in the field. Conditions that enhance pathogen survival are of special concern when assessing their environmental fate and more research is needed on persistent subpopulations (Proctor et al. 2006; Headd and Bradford 2016), regrowth of bacterial pathogens (Zaleski et al. 2005), transformations between active and vegetative phenotypes (Lewis 2007; Veening et al. 2008), and interactions between fecal pathogens and indigenous microbial populations (Hall-Stoodley et al. 2004). However, microcosm studies only consider a limited set of natural conditions, and are therefore not always representative of in situ field measurements of pathogen survival (Sidhu et al. 2015). Consequently, additional research is needed to predict more accurately field-scale survival and their uncertainties.

Pathogens can be transported by advection through soil and groundwater when retention and decay are collectively insufficient to completely remove them from the pore-water. Because an increase in flow velocity produces greater advective transport and less retention of pathogens in porous media, high velocity zones pose an increased risk of rapid pathogen transport at the field-scale. In addition, transport of pathogens can be more rapid than that of solutes because of size exclusion from fine soils and smaller pore spaces with lower or stagnant flow conditions. Many aquifers are characterized by a high degree of physical heterogeneity and exhibit substantive spatial changes in permeability and flow field as a result of layers and lenses of varying soil texture. Much less is known about preferential pathogen transport in fractured rock and karst aquifers and soils characterized by unstable flow, dynamic capillarity, soil structure, macropores from decaying plant roots, burrowing earthworms and animals, and cracks in clayey soils. Experiments in undisturbed soil columns, lysimeters, tile-drains, and the field have frequently revealed that preferential transport pathways are a major contributor to the overall transport of microbes (Zhang et al. 2012; Bradford et al. 2013). More field-based research and modeling is needed to understand better the influence of preferential flow paths on pathogen transport to drinking-water wells and how the resulting information can be used to determine risk assessment more accurately.

A variety of continuum-scale models have been developed to simulate deterministically the transport and fate of pathogens in the subsurface (Bradford et al. 2013, 2014; Molnar et al. 2015). Deterministic models are valuable to analyze experimental data resulting from small-scale transport studies, to test hypotheses regarding factors that control the fate of the pathogens, to improve our understanding of complex processes, and to identify conditions of enhanced risk. Additional model improvements are needed to predict the dependency of pathogen transport on physicochemical conditions, and to quantify and assess the implications of coupled pathogen transport and fate processes. Furthermore, there is still no consensus about the proper conceptual and mathematical description of many transport and fate processes, including the following: size-exclusion; migration adjacent to the solid phase; a non-constant sticking efficiency; reversibility of retention; and release due to variability in physicochemical conditions. Deterministic models can also be employed to simulate field-scale pathogen migration by explicitly accounting for subsurface heterogeneities and the coupling between retention, release, and survival parameters on physicochemical factors. However, deterministic models neglect the considerable uncertainties in the processes controlling transport and fate that are needed to assess risks accurately. Stochastic modeling approaches have been developed to account for uncertainty in flow, transport, and fate processes (Rehmann et al. 1999; Maxwell et al. 2007). Accurate descriptions of field-scale flow, transport, and fate processes and parameters remain a critical challenge for both deterministic and stochastic modeling approaches that seek to improve predictions of field-scale pathogen migration, to advance quantitative microbial risk assessment, and to develop mitigation and best management approaches.

Concluding thoughts

Figure 1 and the following summarize key concepts and research gaps involving pathogens in groundwater. A variety of enteric pathogens are found in fecal wastes. These wastes serve as point or non-point sources of groundwater contamination that has been associated with disease outbreaks. Pathogen concentrations in groundwater are proportional to their abundance in the contamination source. Management and treatment of pathogen sources, therefore, serve as important first barriers to prevent microbial contamination of groundwater; however, existing methods to determine pathogen concentrations in environmental samples are currently laborious, expensive, require specialize equipment and expertise, and only provide semi-quantitative information. Consequently, easily measured microbial indicators are sought for various pathogens. The major conundrum is that some indicators exhibit little correlation with pathogen concentrations in contaminated groundwater and, consequently, should not be used to assess their environmental fate; furthermore, increasing presence of antibiotic resistant bacterial pathogens in groundwater is a topic of emerging concern. Adequate removal of pathogens during passage through soils is, therefore, a critical consideration for safe groundwater production.
Fig. 1

A schematic illustrating keys knowledge gaps that were identified in this paper. Green-colored font indicates conditions or tools that minimize health risks, whereas red font indicates conditions that enhance risks

Elimination of pathogen threats during soil passage can occur as a result of immobilization on the surface of porous or fractured media, or as a result of death and/or inactivation. The pathogen retention rate is commonly found to be larger than the decay rate, so retention is viewed as the main removal mechanism. Many laboratory-scale research studies have been conducted in order to isolate more effectively the influence of specific processes and factors that contribute to pathogen removal. Results demonstrate that pathogen removal is highly dependent on poorly characterized interactions with diverse environmental surfaces and a multitude of physical, chemical, and microbiological factors. Processes that diminish pathogen removal such as reversible retention and enhanced survival, are of particular concern because they substantially increase the risk of groundwater contamination, but remain incompletely investigated. Improved theory and modeling tools are needed to assess the applicability of laboratory data to field application, test hypotheses, understand coupled processes and controlling mechanisms, and to identify conditions of risk.

Natural soil and aquifer environments exhibit great spatial and/or temporal heterogeneity in the physical, chemical, and microbiology properties that strongly influence pathogen transport and fate. This heterogeneity substantially increases the level of complexity and uncertainty in pathogen transport and fate; however, most of the relevant studies involve laboratory column and microcosms. Few studies have attempted to characterize this uncertainty in pathogen transport or removal at the field scale, and approaches to upscale laboratory information to the field-scale are almost nonexistent. Enhanced risks of pathogen transport and groundwater contamination are expected in high velocity zones with little removal. These rapid velocity zones occur in the presence of lenses and layers of high permeability sands and gravels, in rock fractures, in karst systems, and/or due to preferential flow of recharge water through macropores in the vadose zone. Because climate change has been reported to induce more extreme precipitation (recharge) events, the frequency and severity of such preferential flow events are likely to increase pathogen contamination of groundwater, particularly in systems characterized by a high degree of preferential flow. Mathematical models need to account accurately for variability in field-scale flow, transport, and fate processes in order to quantitatively determine risks of pathogen contamination, and to develop mitigation and best management approaches to protect groundwater.

In closing, this paper was written from the perspective of scientists concerned with predicting pathogen transport and fate in groundwater; however, the vast majority of published research on this topic has been conducted at the interface-, pore-, or column-scales. There is frequently a disconnection between findings deriving from laboratory-scale studies and the needs of stakeholders concerned with what happens at the field-scale. For example, drinking water utilities need to safely and cost-effectively provide water, farmers need irrigation water of a quality that does not result in pathogen-contaminated fruits and vegetables, public health officials and government regulators need to be able to monitor groundwater for the presence of pathogens and assess the associated risks to human health, and engineers and consultants often need to site water-supply wells at locations that ensure pathogen removal under highly variable, field-scale conditions. Groundwater flow and processes controlling pathogen retention and release are expected to change spatially and temporally because of field-scale heterogeneity. Consequently, the scientific community needs to do a much better job of upscaling laboratory results to the field-scale, and developing field-scale modeling tools that better account for heterogeneity and uncertainty. Conversely, stakeholders frequently do not adequately communicate their research needs and field-scale observations with research scientists. These stakeholders need to be willing to recognize potential problems through open communication and collaboration with research scientists, proactive monitoring and/or transport modeling, and implementation of best management practices.

Notes

Acknowledgements

We would like to thank Brendan Headd for helpful discussions concerning Fig. 1. This research was supported by the Climate Change, Soils, and Emissions (NP 212) of the USDA-ARS and the Toxics Hydrology Program of the USGS.

References

  1. Akoachere JF, Masalla TN, Njom HA (2013) Multi-drug resistant toxigenic Vibrio cholerae O1 is persistent in water sources in New Bell-Douala, Cameroon. BMC Infect Dis 13(1):366CrossRefGoogle Scholar
  2. Alley WM (2006) Tracking US groundwater: reserves for the future? Environment 48:10–25Google Scholar
  3. Ashbolt NJ, Amézquita A, Backhaus T, Borriello P, Brandt KK, Collignon P, Coors A, Finley R, Gaze WH, Heberer T, Lawrence JR (2013) Human health risk assessment (HHRA) for environmental development and transfer of antibiotic resistance. Environ Health Perspect 121(9):993Google Scholar
  4. Bech TB, Rosenbom AE, Kjaer J, Amin MM, Olsen P, Jacobsen CS (2014) Factors influencing the survival and leaching of tetracycline-resistant bacteria and Escherichia coli through structured agricultural fields. Agric Ecosyst Environ 195:10–17Google Scholar
  5. Beer KD, Gargano JW, Roberts VA, Hill VR, Garrison LE, Kutty PK, Hilborn ED, Wade TJ, Fullerton KE, Yoder JS (2015) Surveillance for waterborne disease outbreaks associated with drinking water: United States, 2011–2012. MMWR Morb Mortal Wkly 64:842–848CrossRefGoogle Scholar
  6. Binder S, Levitt AM, Hughes JM (1999) Preventing emerging infectious diseases as we enter the 21st century: CDC’s strategy. Public Health Rep 114(2):130–134CrossRefGoogle Scholar
  7. Blackburn BG, Craun GF, Yoder JS, Hill V, Calderon RL, Chen N, Lee SH, Levy DA, Beach MJ (2004) Surveillance for waterborne-disease outbreaks associated with drinking water: United States, 2001–2002. MMWR Surveill Summ 53(8):23–45Google Scholar
  8. Böckelmann U, Dörries HH, Ayuso-Gabella MN, de Marçay MS, Tandoi V, Levantesi C, Masciopinto C, Van Houtte E, Szewzyk U, Wintgens T, Grohmann E (2009) Quantitative PCR monitoring of antibiotic resistance genes and bacterial pathogens in three European artificial groundwater recharge systems. Appl Environ Microbiol 75(1):154–163CrossRefGoogle Scholar
  9. Borchardt MA, Bradbury KR, Alexander EC, Kolberg RJ, Alexander SC, Archer JR, Braatz LA, Forest BM, Green JA, Spencer SK (2011) Norovirus outbreak caused by a new septic system in a dolomite aquifer. Ground Water 49(1):85–97CrossRefGoogle Scholar
  10. Bradford SA, Torkzaban S (2015) Determining parameters and mechanisms of colloid retention and release in porous media. Langmuir 31(44):12096–12105CrossRefGoogle Scholar
  11. Bradford SA, Morales VL, Zhang W, Harvey RW, Packman AI, Mohanram A, Welty C (2013) Transport and fate of microbial pathogens in agricultural settings. Crit Rev Environ Sci Technol 43(8):775–893CrossRefGoogle Scholar
  12. Bradford SA, Wang Y, Kim H, Torkzaban S, Šimůnek J (2014) Modeling microorganism transport and survival in the subsurface. J Environ Qual 43(2):421–440CrossRefGoogle Scholar
  13. Bradford SA, Kim H, Headd B, Torkzaban S (2016) Evaluating the transport of bacillus subtilis spores as a potential surrogate for cryptosporidium parvum oocysts. Environ Sci Technol 50:1295–1303CrossRefGoogle Scholar
  14. Cho HG, Lee SG, Kim WH, Lee JS, Park PH, Cheon DS, Jheong WH, Jho EH, Lee JB, Paik SY (2014) Acute gastroenteritis outbreaks associated with ground-waterborne norovirus in South Korea during 2008–2012. Epidemiol Infect 142(12):2604–2609CrossRefGoogle Scholar
  15. Craun GF (2012) The importance of waterborne disease outbreak surveillance in the United States. Ann Ist Super Sanita 48(4):447–459CrossRefGoogle Scholar
  16. Craun GF, Brunkard JM, Yoder JS, Roberts VA, Carpenter J, Wade T, Calderon RL, Roberts JM, Beach MJ, Roy SL (2010) Causes of outbreaks associated with drinking water in the United States from 1971 to 2006. Clin Microbiol Rev 23(3):507–528CrossRefGoogle Scholar
  17. Daszak P, Epstein JH, Kilpatrick AM, Aguirre AA, Karesh WB, Cunningham AA (2007) Collaborative research approaches to the role of wildlife in zoonotic disease emergence. In: Wildlife and emerging zoonotic diseases: the biology, circumstances and consequences of cross-species transmission. Springer, Heidelberg, Germany, pp 463–475CrossRefGoogle Scholar
  18. Economides C, Liapi M, Makris KC (2012) Antibiotic resistance patterns of Salmonella and Escherichia coli in the groundwater of Cyprus. Environ Geochem Health 34(4):391–397CrossRefGoogle Scholar
  19. Ferguson AS, Layton AC, Mailloux BJ, Culligan PJ, Williams DE, Smartt AE, Sayler GS, Feighery J, McKay LD, Knappett PS, Alexandrova E (2012) Comparison of fecal indicators with pathogenic bacteria and rotavirus in groundwater. Sci Total Environ 431:314–322CrossRefGoogle Scholar
  20. Fong TT, Mansfield LS, Wilson DL, Schwab DJ, Molloy SL, Rose JB (2007) Massive microbiological groundwater contamination associated with a waterborne outbreak in Lake Erie, South Bass Island, Ohio. Environ Health Perspect 115:856–864CrossRefGoogle Scholar
  21. Gallay A, De Valk H, Cournot M, Ladeuil B, Hemery C, Castor C, Bon F, Megraud F, Le Cann P, Desenclos JC (2006) A large multi‐pathogen waterborne community outbreak linked to faecal contamination of a groundwater system, France, 2000. Clin Microbiol Infect 12(6):561–570CrossRefGoogle Scholar
  22. Gerba CP, Smith JE (2005) Sources of pathogenic microorganisms and their fate during land application of wastes. J Environ Qual 34(1):42–48Google Scholar
  23. Gerba CP, Blair BL, Sarkar P, Bright KR, MacLean RC, Marciano-Cabral F, Ortega-Pierres G, Cacciò S, Fayer R, Mank TG, Smith HV (2009) Occurrence and control of Naegleria fowleri in drinking water wells, chap 19. In: Ortega-Pierres G, Caccio S, Fayer R, Mank TG, Smith HW, Thompson RCA (eds) Giardia and cryptosporidium: from molecule to disease. CAB, Oxfordshire UK, pp 238–247Google Scholar
  24. Giammanco GM, Di Bartolo I, Purpari G, Costantino C, Rotolo V, Spoto V, Geraci G, Bosco G, Petralia A, Guercio A, Macaluso G (2014) Investigation and control of a Norovirus outbreak of probable waterborne transmission through a municipal groundwater system. J Water Health 12(3):452–464CrossRefGoogle Scholar
  25. Ginn TR, Wood BD, Nelson KE, Scheibe TD, Murphy EM, Clement TP (2002) Processes in microbial transport in the natural subsurface. Adv Water Resour 25(8):1017–1042CrossRefGoogle Scholar
  26. Guzman-Herrador B, Carlander A, Ethelberg S, de Blasio BF, Kuusi M, Lund V, Lofdahl M, MacDonald E, Nichols G, Schonning C, Sudre B (2015) Waterborne outbreaks in the Nordic countries, 1998 to 2012. Eurosurveillance: Eur Commun Dis Bull 20:24CrossRefGoogle Scholar
  27. Hall-Stoodley L, Costerton JW, Stoodley P (2004) Bacterial biofilms: from the natural environment to infectious diseases. Nat Rev Microbiol 2(2):95–108CrossRefGoogle Scholar
  28. Headd B, Bradford SA (2016) Use of aerobic spores as a surrogate for cryptosporidium oocysts in drinking water supplies. Water Res 90:185–202CrossRefGoogle Scholar
  29. Howard KWF (2006) Microbial pollution of groundwater in the town of Walkerton, Canada, in urban groundwater management and sustainability. Springer, Netherlands, pp 315–330CrossRefGoogle Scholar
  30. Hsu TTD, Lee J (2015) Global distribution and prevalence of Arcobacter in food and water. Zoonoses Public Health 62(8):579–589CrossRefGoogle Scholar
  31. Hynds PD, Thomas MK, Pintar KD (2014) Contamination of groundwater systems in the US and Canada by enteric pathogens, 1990–2013: a review and pooled-analysis. PLoS One 9(5):e93301CrossRefGoogle Scholar
  32. Jakopanec I, Borgen K, Vold L, Lund H, Forseth T, Hannula R, Nygård K (2008) A large waterborne outbreak of campylobacteriosis in Norway: the need to focus on distribution system safety. BMC Infect Dis 8(1):1CrossRefGoogle Scholar
  33. Jin Y, Flury M (2002) Fate and transport of viruses in porous media. Adv Agron 77:39–102CrossRefGoogle Scholar
  34. Kang DK, Ali MM, Zhang KX, Huang SS, Peterson E, Digman MA, Gratton E, Zhao WA (2014) Rapid detection of single bacteria in unprocessed blood using integrated comprehensive droplet digital detection. Nat Commun 5:5427. doi:10.1038/ncomms6427 CrossRefGoogle Scholar
  35. Kim SH, Cheon DS, Kim JH, Lee DH, Jheong WH, Heo YJ, Chung HM, Jee Y, Lee JS (2005) Outbreaks of gastroenteritis that occurred during school excursions in Korea were associated with several waterborne strains of norovirus. J Clin Microbiol 43(9):4836–4839CrossRefGoogle Scholar
  36. Lazcka O, Del Campo FJ, Munoz FX (2007) Pathogen detection: a perspective of traditional methods and biosensors. Biosens Bioelectron 22(7):1205–1217CrossRefGoogle Scholar
  37. Lewis K (2007) Persister cells, dormancy and infectious disease. Nat Rev Microbiol 5(1):48–56CrossRefGoogle Scholar
  38. Maupin MA, Barber N (2005) Estimated withdrawals from principal aquifers in the United States. US Geol Surv Circ 1279Google Scholar
  39. Maxwell RM, Welty C, Harvey RW (2007) Revisiting the Cape Cod bacteria injection experiment using a stochastic modeling approach. Environ Sci Technol 41(15):5548–5558CrossRefGoogle Scholar
  40. Molnar IL, Johnson WP, Gerhard JI, Willson CS, O’Carroll DM (2015) Predicting colloid transport through saturated porous media: a critical review. Water Resour Res 51(9):6804–6845CrossRefGoogle Scholar
  41. Murphy HM, Pintar KD, McBean EA, Thomas MK (2014) A systematic review of waterborne disease burden methodologies from developed countries. J Water Health 12(4):634–655CrossRefGoogle Scholar
  42. Pazmino E, Trauscht J, Dame B, Johnson WP (2014) Power law size-distributed heterogeneity explains colloid retention on soda lime glass in the presence of energy barriers. Langmuir 30(19):5412–5421CrossRefGoogle Scholar
  43. Proctor RA, Von Eiff C, Kahl BC, Becker K, McNamara P, Herrmann M, Peters G (2006) Small colony variants: a pathogenic form of bacteria that facilitates persistent and recurrent infections. Nat Rev Microbiol 4(4):295–305CrossRefGoogle Scholar
  44. Ramírez-Castillo FY, Loera-Muro A, Jacques M, Philippe G, Avelar-González FJ, Harel J, Guerrero-Barrera AL (2015) Waterborne pathogens: detection methods and challenges. Pathogens 4(2):307–334CrossRefGoogle Scholar
  45. Rehmann LL, Welty C, Harvey RW (1999) Stochastic analysis of virus transport in aquifers. Water Resour Res 35(7):1987–2006CrossRefGoogle Scholar
  46. Rogan WJ, Brady MT (2009) Drinking water from private wells and risks to children. Pediatrics 123(6):e1123–e1137CrossRefGoogle Scholar
  47. Ryan M, Hamilton K, Hamilton M, Haas CN (2014) Evaluating the potential for a Helicobacter pylori drinking water guideline. Risk Anal 34(9):1651–1662Google Scholar
  48. Schijven JF, Hassanizadeh SM (2000) Removal of viruses by soil passage: overview of modeling, processes, and parameters. Crit Rev Environ Sci Technol 30(1):49–127CrossRefGoogle Scholar
  49. Sidhu JP, Toze S, Hodgers L, Barry K, Page D, Li Y, Dillon P (2015) Pathogen decay during managed aquifer recharge at four sites with different geochemical characteristics and recharge water sources. J Environ Qual 44(5):1402–1412CrossRefGoogle Scholar
  50. Sobsey MD, Khatib LA, Hill VR, Alocilja E, Pillai S (2001) Pathogens in animal wastes and the impacts of waste management practices on their survival, transport and fate: white papers on animal agriculture and the environment. MidWest Plan Service (MWPS), Iowa State University, Ames, IAGoogle Scholar
  51. Stevenson ME, Blaschke AP, Schauer S, Zessner M, Sommer R, Farnleitner AH, Kirschner AKT (2014) Enumerating microorganism surrogates for groundwater transport studies using solid-phase cytometry. Water Air Soil Pollut 225:1827CrossRefGoogle Scholar
  52. Torkzaban S, Bradford SA (2016) Critical role of surface roughness on colloid retention and release in porous media. Water Res 88:274–284CrossRefGoogle Scholar
  53. Toze S (1999) PCR and the detection of microbial pathogens in water and wastewater. Water Res 33(17):3545–3556CrossRefGoogle Scholar
  54. Treumann S, Torkzaban S, Bradford SA, Visalakshan RM, Page D (2014) An explanation for differences in the process of colloid adsorption in batch and column studies. J Contam Hydrol 164:219–229CrossRefGoogle Scholar
  55. Tufenkji N, Emelko MB (2011) Fate and transport of microbial contaminants in groundwater. Encycl Environ Health 2:715–726CrossRefGoogle Scholar
  56. US Environmental Protection Agency (2006) National primary drinking water regulations: ground water rule. Fed Regist 71:65574–65660Google Scholar
  57. US Environmental Protection Agency (2010a) Impaired waters and total maximum daily loads. US EPA, Washington, DCGoogle Scholar
  58. US Environmental Protection Agency (2010b). Long term 2 enhanced surface water treatment rule toolbox guidance manual, EPA 815-R-0e16, US EPA, Washington, DCGoogle Scholar
  59. Veening JW, Smits WK, Kuipers OP (2008) Bistability, epigenetics, and bet-hedging in bacteria. Annu Rev Microbiol 62:193–210CrossRefGoogle Scholar
  60. Wallender EK, Ailes EC, Yoder JS, Roberts VA, Brunkard JM (2014) Contributing factors to disease outbreaks associated with untreated groundwater. Groundwater 52(6):886–897CrossRefGoogle Scholar
  61. Wong K, Fong TT, Bibby K, Molina M (2012) Application of enteric viruses for fecal pollution source tracking in environmental waters. Environ Int 45:151–164CrossRefGoogle Scholar
  62. Zaleski KJ, Josephson KL, Gerba CP, Pepper IL (2005) Survival, growth, and regrowth of enteric indicator and pathogenic bacteria in biosolids, compost, soil, and land applied biosolids. J Residuals Sci Technol 2(1):49–63Google Scholar
  63. Zhang W, Tang X, Weisbrod N, Guan Z (2012) A review of colloid transport in fractured rocks. J Mt Sci 9(6):770–787CrossRefGoogle Scholar

Copyright information

© Springer-Verlag Berlin Heidelberg (outside the USA) 2016

Authors and Affiliations

  1. 1.USDA-ARS, US Salinity LaboratoryRiversideUSA
  2. 2.USGSBoulderUSA

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