July 31, 2017
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Pitkanen, T. and Hanninen, M-L. 2017. Members of the family Campylobacteraceae: Campylobacter jejuni, Campylobacter coli. In: J.B. Rose and B. Jiménez-Cisneros, (eds) Global Water Pathogen Project. http://www.waterpathogens.org (A. Pruden, N. Ashbolt and J. Miller (eds) Part 3 Bacteria) http://www.waterpathogens.org/book/campylobacter Michigan State University, E. Lansing, MI, UNESCO.
Acknowledgements: K.R.L. Young, Project Design editor; Website Design: Agroknow (http://www.agroknow.com)
|Last published: July 31, 2017|
Campylobacter infection is one the most widely spread bacterial gastroenteric disease worldwide. The global estimate of the burden of campylobacteriosis for 2010 was 7.5 million disability-adjusted life years (DALYs). The knowledge of the incidence, prevalence, clinical output and epidemiology of Campylobacter as a common cause of human acute gastroenteritis has been published since 1977, but the coverage of prevalence and incidence data from different parts of the world is still highly variable. In the industrialized countries, the number of reported cases has increased during the last 10 to 15 years. However, national statistics underestimate the actual population incidence because only a fraction of the Campylobacter cases present to health services, and many of these are not investigated further. In addition, co-infections with other enteric pathogens are common. In high-income regions, the most common symptoms of a Campylobacter infection include an acute, self-limiting gastroenteritis, with an incubation period of 2 to 5 days. In developing regions, watery diarrhea is the most common presentation of the illness, commonly seen during the first years of life. In the latter regions, due to the endemic nature and acquired immunity after the repeated exposure to Campylobacter, adults are only infrequently affected.
Currently, 29 species and 12 subspecies are classified in the genus Campylobacter. The most important Campylobacter species in human gastroenteritis is Campylobacter jejuni, which accounts for 90 to 95% of all campylobacteriosis cases reported. The majority of the remaining cases are caused by Campylobacter coli, but the importance of C. coli as an enteric pathogen varies between regions. The role of some other species (Campylobacter lari, Campylobacter upsaliensis, Campylobacter concisus) is less well characterized. Based on the data of experimental infections and indirectly from waterborne outbreaks, it is known that exposure to only a few hundred cells may result in illness. Due to uncertainties in estimating the dose-response relation at the typically low doses from water exposures, risk estimations for C. jejuni exposures are highly uncertain, and in the absence of dose-response data for C. coli or other Campylobacter species, not directly possible.
A wide variety of animals, especially poultry, wild birds, cattle and sheep carry high numbers of C. jejuni and C. coli as commensals in their intestines, all being potential reservoirs. Fecal contamination of food, recreational water and drinking water contributes to human infections and the fecal material of infected persons (symptomatic and asymptomatic) spread the organisms back to environment through sewage plants and toilets. Reported Campylobacter numbers in non-disinfected wastewater effluents vary between 100 and 100,000 CFU/ L. Campylobacter are frequently isolated from surface waters from different parts of the world despite the fact that the isolation of Campylobacter from water requires specialized culture-based techniques and may fail due to insufficient method sensitivity or difficulties in separation of Campylobacter from the non-target bacteria. The potential false negative results due to the occurrence of viable-but-not-culturable Campylobacter and other difficult to culture situations has facilitated the development of nucleic acid-based molecular Campylobacter detection methods.
Mechanisms that enable Campylobacter to survive in the environment are poorly understood. Different survival characteristics and abilities of Campylobacter species under environmental conditions affect our understanding of Campylobacter ecology and diversity. For example, it has been reported that C. lari can survive better in aquatic environments than C. jejuni and C. coli. The survival of Campylobacter is favoured by low temperature, the absence of sunlight and by low numbers of indigenous microbiota. In general, it can be assumed that the same water purification techniques that are capable of removing Escherichia coli from water, remove or inactivate Campylobacter cells as efficiently. The exact Campylobacter removal rates, however, remain unknown due to the semi-quantitative nature of the Campylobacter detection methods.
Campylobacteriosis is one the most common bacterial gastroenteric diseases worldwide (Blaser, 1997; Murray et al., 2012; Scallan et al., 2015). Most infections are sporadic and outbreaks are rather uncommon. Since, Skirrow (1977) published data showing C. jejuni was a much more common cause of human acute gastroenteritis than previously estimated, data on the incidence, prevalence and epidemiology has vastly improved, yet data is still highly variable. Most reliable data based on notification requirement of transmissible infectious diseases to public health authorities relates to developed countries where surveillance systems have been active for a long time (e.g. Member States of European Union, United States of America and Canada). On the other hand less detailed and unsystematic data production systems are available from developing regions that still provide useful data.
The global estimate of the burden of campylobacteriosis for 2010 was 7.5 million disability-adjusted life years (DALYs). This was a clear improvement from 1990, when the burden of campylobacteriosis was estimated to be 16.6 million DALYs. However, Campylobacter enteritis accounted for 8.5% of the total burden of diarrheal disease, ranking fourth after rotavirus, cryptosporidiosis and Escherichia coli diarrhea (combined enterotoxigenic and enteropathogenic E. coli infections) (Murray et al., 2012). Thus, Campylobacter remains one of the most frequently occurring bacterial causes of gastrointestinal diseases worldwide. Several countries have performed country-level analyses of DALYs. In the USA in 2006, 845,000 people were estimated to have acquired domestic Campylobacter infection and the estimated DALY was 22,500 (10,400 to 38,600; 90% Credible Interval, population size approx. 325 million). In this number the sequelae (IBD, Guillan-Barre/Miller Fisher syndromes, and reactive arthritis) increased the years of life disabled (YLD) by more than 70% of the total DALY (Scallan et al., 2015). Further, in the Netherlands (population approx. 17 million; estimated number of cases 108,000 (33,000–271,000) Campylobacter DALY was estimated for 2011 to be 3,633 (Mangen et al., 2015). In Australia (population 22 million, Campylobacter cases 774,003) estimated DALY for 2010 was 18 222 showing very high impact on public health (Gibney et al., 2014).
An overview on global distribution of reported campylobacteriosis cases is presented in Table 1. The epidemiology and demography of Campylobacter infections differs between developing and industrialized countries. In developing countries, symptomatic disease is most commonly seen only during the first two years of life, and symptomatic illness in adults is rare due to the endemic nature of Campylobacter in these regions. The clinical picture also differs from that seen in industrialized countries, as watery diarrhea is the most common presentation. The peak in the very young and lack of clinical illness in adults is believed to be due to acquired immunity after repeated exposure to Campylobacter, and supporting this a high percentage of asymptomatic seropositive individuals have been reported in several studies (Blaser, 1997; Kirkpatrick and Tribble, 2011; Platts-Mills et al., 2015). In addition, co-infection with other enteric pathogens is relatively common. In developing countries monitoring data is poorly available. In a recent, prospective, multi-center, case-control study of acute moderate severe diarrhea in children (Enterics Multi-Center Study, GEMS), using culture based techniques Campylobacter spp. were found to be in the top five causes in Bangladesh, Pakistan and India among 2 to 5 year olds (Kotloff et al., 2013; Platts-Mills et al., 2015).
Most countries in Europe and North America have existing annual reporting and notification systems for incidence/prevalence of campylobacteriosis indicating that reliable data on prevalence of the infections among populations exists as well as trends of infections during longer periods of time are available. These trend data from Europe and North America have shown that the number of reported cases has increased during the last 10 to 15 years (EFSA, 2015; MMWR, 2014; Thomas et al., 2013). The data collection also includes information on the prevalence of C. jejuni and C. coli in their domestic animal reservoirs and certain foods improving assessment of potential sources of human infections. Some countries also have data on foreign travel-associated cases separated from those acquired from domestic sources (EFSA, 2015; Nichols et al., 2012; Kendall et al., 2012). This travel-associated data is important for targeting potential interpretation measures to decrease health burden of the illness. The incidence/prevalence data available from low-income countries is often lacking or fragmented but data collected from different sources indicate that the epidemiology of campylobacteriosis is different than in developed regions (Kotloff et al., 2013; Mason et al., 2013).
The European Union (EU) notification rate of campylobacteriosis was 64.8 per 100,000 population in 2013, but varied considerably between the member states (MS); from <2 to 173.7 per 100,000 population in Latvia and Czech Republic, respectively (Table 1), indicating the surveillance is not similarly developed within the EU countries. However, the true incidence of Campylobacter infection is higher than reported. The national statistics grossly underestimate the actual population incidence because only a fraction of the campylobacteriosis cases are presented to health services, and many of these are not investigated further. For instance in the UK, Tam et al. (2012) reported that every campylobacteriosis case reported to the national surveillance represented 9.3 community campylobacteriosis cases between 2008 and 2009. Overall, the true incidence is expected to range between 4.4 and 9.3 per 1,000 person-years population in high-income countries. The underreporting level varies between countries depending on functionality of the surveillance system.
The most important Campylobacter species in human gastroenteritis is Campylobacter jejuni, which accounts for 90 to 95% of all campylobacteriosis cases identified. The majority of the remaining cases are caused by Campylobacter coli, but the importance of C. coli as an enteric pathogen varies between regions, degree of urbanization and age of the patient suggesting that the epidemiology of C. coli infection differs among countries (Blaser, 1997). However, the predominance of C. jejuni and C. coli may be biased by the selective cultivation media employed (Lastovica and Allos, 2008). The role of some other species (Campylobacter fetus, Campylobacter lari, Campylobacter upsaliensis, Campylobacter concisus) is less well characterized, especially their role in infections in developing countries.
In high-income regions, the most common symptoms of a Campylobacter infection include an acute, self-limiting gastroenteritis, and the incubation period is typically 2 to 5 days (Blaser, 1997; Skirrow and Blaser, 2000), but up to 8 days has been reported. Half of the patients experience a febrile period with fever, malaise and abdominal pain preceding the diarrhea. Fresh blood in the stool is common, while vomiting occurs in approximately 15% of the cases. The pathological lesions seen in humans suffering from Campylobacter infection include acute inflammatory enteritis extending to colon and rectum, with terminal ileitis and colitis (Blaser, 1997). Short lasting immunity to homologous strains has been reported, and immunity has been reported under natural conditions, for instance after repeated occupational exposure. Normally the diarrhea lasts for 2 to 3 days, while discomfort can persist for weeks. The most severe cases, however, need hospitalization (Feodoroff et al., 2010). The incidence peaks in young children and again during early adulthood. In developing countries, C. jejuni infections are common in the very young children (< 5 years), causing watery diarrhea (Lengerh et al., 2013), while adults are only infrequently affected due to acquired immunity (Kotloff et al., 2013; Allos, 2001). Only a few hundred cells are thought to cause infections (Robinson, 1981), but as no dose-response for symptoms was detected (Black et al., 1988) interpretation of the infectious dose from the data of experimental infections is complicated because, interpretation of the conditional fraction that go onto disease was problematic. Medema et al., (1996) using the experimental data of Black et al., (1988) fitted it to a Beta-Poisson dose-response model but considered the low dose data too unreliable to be of value (further discussion of appropriate dose-response models and parameter estimates can be found in chapter Risk Assessment for Sanitation). While data on the infectious dose of C. coli are not available from human volunteer studies, data from waterborne outbreaks suggests the infection dose is low (Guzman-Herrador et al., 2015).
The most severe, but rare complication following a C. jejuni infection is Guillain-Barré syndrome (GBS) (incidence in developed regions range from 0.4 to 4.0 cases per 100,000), a postinfectious autoimmune disorder of the peripheral nervous system. Up to 20% of the patients having GBS require mechanical ventilation. However, mortality rates of GBS have been reduced to 2 to 3% in the developed regions, although it remains higher in less developed area (Allos, 1997; Tam et al., 2007). Reactive arthritis is another complication following 1% to 5% of campylobacteriosis cases, and mainly affects the bigger joints, but even the smaller joints can be involved (Hannu et al., 2002; Townes, 2010). Other rare complications include extra-intestinal infections and bacteremia, occurring mainly in immune-compromised patients. Furthermore, several studies have reported an association between C. jejuni infection and post-infectious irritable bowel syndrome (IBS) as well as inflammatory bowel disease (IBD) (Marshall et al., 2006; Kirkpatrick and Tribble, 2011). These post-infectious complications increase the DALY of the disease.
The family Campylobacteraceae includes the genera Arcobacter, Sulfurospirillum, Dehalospirillum and Campylobacter and are Gram-negative, generally microaerophilic organisms with a low G+C content and a relatively small genome. Currently, 29 species and 12 subspecies are classified in the genus Campylobacter, of which seven species and one subspecies were described after 2009 (http://www.bacterio.net/campylobacter.html, accessed 02.04.2015). A majority of the species are animal commensals colonising the reproductive organs, lower parts of intestinal tract or oral cavity. Several species are opportunistic or primary zoonotic pathogens. Two most clinically important species in human infections are C. jejuni (two subspecies, C. jejuni subsp. jejuni and C. jejuni subsp. doylei) and C. coli. The pathogenic role of C. jejuni subsp. doylei is unclear, but it has been isolated from infants with bacteremia. The two subspecies differ biochemically and can be separated by polymerase chain reaction (PCR) of nitrate reductase locus (Miller et al., 2007).
Campylobacter spp. are spiral curved rods with a polar flagellum occurring at one end of the cell that enables the display of rapid corkscrew-like darting and spinning motions (Butzler, 2004; Debruyne et al., 2008). C. jejuni is microaerophilic and a slender, spirally curved, non-spore forming, Gram-negative rod, which measures 0.2 to 0.8 µm wide and 0.5 to 5 µm long. In older cultures or in unfavorable environments, coccoid forms of C. jejuni cells are seen. Thermotolerant Campylobacter spp. are able to grow at 42°C but not below 30°C, and this group includes the species C. jejuni, C. coli, C. lari and C. upsaliensis (ISO 17995, 2005). C. jejuni cannot utilize carbohydrates for energy (some strains utilize fucose), but rather uses amino acids and tricarboxylic acid cycle intermediates as primary energy source (Debruyne et al., 2008). C. lari strains, often isolated from wild birds and surface water, have been differentiated from C. jejuni and C. coli due to their resistance to nalidixic acid (Debruyne et al., 2008). Traditional phylogenetic analysis to describe the taxonomy of Campylobacter spp. is based on the similarity of 16S rRNA gene (Debruyne et al., 2008).
Most human Campylobacter infections are thought to be food- or waterborne (Allos, 2001; Guzman-Herrador et al., 2015; Mughini Gras et al., 2012; Pitkänen, 2013). C. jejuni and C. coli are zoonotic pathogens which have a broad variety of different animal hosts (Wagenaar et al., 2015). This extremely broad host spectrum from domestic and pet animals through mammalian wildlife to wild birds gives for this organism an almost unique position among zoonotic pathogens and makes detection of all potential sources and transmission routes very complicated. Fecal contamination of the food chain and environment transmits Campylobacter to human foods, recreational water and drinking water. Further, fecal material of infected persons (symptomatic and asymptomatic) spread the organisms back to environment through human excreta and sewage systems. Fecal input is high and increases the possibility that susceptible humans will become infected by fecal-oral route through contaminated food and water both in highly developed as well as in less developed regions. Direct contact with animals is also a likely route of transmission. Fly borne transmission has also been postulated. Person-to person transmission is infrequent and has only been described in young children (Butzler, 2004). A diagram emphasizing the cyclic nature of C. jejuni and C. coli transmission from animal reservoirs and human excreta through food and water environment is presented in Figure 1.
Figure 1. Cyclic nature of Campylobacter spp. transmission from animal reservoirs to humans through fecal contamination of food and water. Adapted with permission from Christian Penny, LIST, Luxembourg
A wide variety of animal species carry C. jejuni and C. coli as commensals in their intestines, being potential reservoirs and sources of human infections (Ogden et al., 2009). During the last 10 to 15 years when modern population genetic tools, such as multilocus sequencing typing (MLST) has been more systematically applied to characterize Campylobacter populations colonizing different animal species and human patients, new information on the role of different animal species as reservoir/source has accumulated (Kärenlampi et al., 2007). These studies often show that certain animal species are more often colonized with MLST types overlapping with of those of human patients (generalist types) indicating that they could be a reservoir/source (de Haan et al., 2010; Sheppard et al., 2009; Lévesque et al., 2013). Further source attribution models combining MLST data and mathematical modeling indicate which animal reservoirs play the most important role in human infections (Mughini-Gras et al., 2012; de Haan et al., 2010). Several animal species also have MLST types which are strictly associated with the host. These types do not commonly occur in other animal species or human patients (host-adapted types) and they can be regarded as less virulent even though more data will be required for final conclusions (Cody et al., 2015; Llarena et al, 2015a). The most relevant reservoirs/sources of human infections are presented next.
In addition to avian sources, dairy and beef cattle are typically colonized by C. jejuni and C. hyointestinalis. Colonization is age dependent with young animals are more often carrying C. jejuni than older animals. Both slaughterhouse surveys as well farm studies show variations in prevalence (between 12.5% and 89.4%) depending on study (Wesley et al., 2000; Nielsen, 2002; Gilpin et al., 2008; Kwan et al., 2008; Hakkinen et al., 2007). Within-herd prevalence, similarly, will vary depending on study site from 0% to 100% in dairy cattle (Gilpin et al., 2008; Pradhan et al., 2009; Hakkinen et al., 2007), and from 5.4% to 83% in beef cattle (Inglis et al., 2004; Berry et al., 2006; Oporto et al., 2007). The bacterial counts in bovine fecal samples are usually low (< 103 per gram) and therefore often detected only by enrichment (range in different studies: not detected up to 106 per gram) but temporary fluctuations in counts are common. In different source attribution models bovine as source has presented approximately 20 to 40%. Raw milk-associated outbreaks are common indicating that C. jejuni strains colonizing cattle are capable of infecting humans. Further, reports from case-control studies have also identified the consumption of unpasteurised milk as an important risk factor for campylobacteriosis among humans (Studahl and Andersson, 2000; Kapperud et al., 2003; Neimann et al., 2003; Michaud et al., 2004) as well as handling raw beef (Schönberg-Norio et al., 2004). Molecular epidemiological studies have shown overlapping genotypes between cattle and humans further revealing that cattle can be a source of human infection. Certain MLST types such as ST-61 have adapted to cattle, but are also able to cause symptomatic infections in humans. Also sheep can be colonized by C. jejuni and C. coli genotypes overlapping with those isolated from human patients, as reported in Scotland (Sheppard et al., 2009). In principle several other animal species carrying Campylobacter spp. can be source of human infections but these are usually sporadic cases.
Epidemiology studies performed during the last 30 years clearly indicate that poultry, especially, chickens are one of the most important reservoirs/sources of human campylobacteriosis worldwide (Skirrow, 1977; Llarena et al., 2015; Wagenaar et al., 2015). According to recent evaluation by EU Biohazard Panel (EFSA, 2011), 20 to 30% of human Campylobacter infections in the EU member states can be explained by handling and consumption of contaminated chicken meat (direct exposure), but chicken production as whole plays major role (explains 30 to 50% of cases) because chicken production acts as amplification and generation site of Campylobacter (reservoir). The bacteria can spread from farms, slaughterhouses and through other routes to the environment, causing human exposure through environmental vehicles (Figure 1). The reason why poultry is an important source of C. jejuni and also C. coli is that their prevalence in commercial flocks is up to 70% in many industrialized countries, yet there are significant spatial and temporal differences in prevalence (EFSA, 2015; Kovats et al., 2005). In industrialized countries chickens are produced in units containing 10,000 to 50,000 birds per a house and a farm can have several houses where birds are reared for five to seven weeks (differences in the breeding times exist). Commonly if a flock is Campylobacter positive, all birds carry the bacterium in their intestines, at concentrations up to 108 per gram of fecal material at time of slaughter. Industrialized production cycles have usually strict biosecurity control systems protecting the production from contamination. However, the capability to have high biosecurity level during all production steps is challenging. Biosecurity also includes the safe handling of the animal waste including manure and slaughterhouse waste, which are treated in scheduled ways to prevent pathogens (Campylobacter spp.) spreading to the outside environment (EFSA, 2011).
The UN report’s the world’s stock of chickens was 19 billion in 2012, meaning almost three chickens per a human being (http://www.thepoultrysite.com/focus/global-poultry-trends/2400/global-poultry-trends-region-select-track-poultry-trends-across-the-world, accessed 07.02.2016). The production is centralized: 50% of the poultry production takes place in tree countries, USA, Brazil and China. In the EU, approximately 6 million chickens are slaughtered each year. The production is local but the market is global meaning that the ecology of Campylobacter is mostly local concerning the transmission of the strains but also spreading globally through exported meat contaminated by Campylobacter. On the other hand free range and organic production systems are increasing and may cause even higher contamination risks in production. The situation in rural developing areas can be different because on those regions poultry production often happens at small scale at family-own farms where humans, poultry and other animals are living in close contact (backyard rearing) making the spreading of Campylobacter strains between different hosts and the environment including water a common phenomenon.
Wild birds are a huge diverse group of different bird species with differing ecologies and life styles that also represent an important reservoir and source of Campylobacter species causing human infections (Cody et al., 2015; Llarena et al., 2015a; Muchini-Gras et al., 2012; Kwan et al., 2014; Griekspoor et al., 2013). They can cause a direct transmission through their use as foods or transmit indirectly by contaminating foods, bathing water or drinking water reservoir by fecal material and they can work as reservoirs to transmit Campylobacter spp. to domestic and other wild animals (Wagenaar et al., 2015). There are both bird species which have their life cycles locally and species which migrate long distances and are then able to transmit Campylobacter spp. between distantly located areas. Studies performed on different areas in the world from all continents to Antarctica reveal that Campylobacter spp. are widely spread among wild birds (Griekspoor et al., 2013). Several Campylobacter species colonize birds, most important are C. jejuni, C. coli and C. lari, a bird-adapted species. Most studies are targeted on wild birds as reservoir transferring Campylobacter spp. to domestic animals or humans. Bird species seem to differ how commonly they carry Campylobacter spp.; some have high prevalence and some low or nonexistent colonization. Bird species known to be commonly colonized are ducks (family Anatidae), shorebirds (several families), corvids, gulls, pigeons, doves, thrushes and starlings (Griekspoor et al., 2013). Bird species which are living in close connection to agriculture and other human activities (urban areas, close to landfills etc.) seem to be often colonized. Epidemiological studies show evidence that fecal contamination of non-disinfected drinking water by wild bird feces has been associated to some waterborne outbreaks (Pitkänen et al., 2008). However, comparison of wild bird and human patient isolates seldom indicate overlapping sero- or genotypes thus making final conclusion on the role of wild birds as contamination sources unclear. Modern molecular genotyping methods are applied and used to compare similarity of genotypes of wild birds and human patients or domestic animals. MLST typing in combination with mathematical source attribution models have been applied and they generally show that some types overlap between humans, animals and birds (ST-45, ST-48, ST-21 and ST-257) but birds also have types which seem to be unique for the species (e.g. ST 1034 in barnacle geese (Llarena et al., 2015a). Interestingly the bird-associated MLST types occur in certain bird species all over the world further supporting the idea on host-associated types. A recent UK study using MLST typing data and a mathematical model estimated that wild bird-attributed isolates could account annually for 2 to 3% of human cases in Oxfordshire, UK (Cody et al., 2015). Also isolated outbreaks point to human-infectious C. jejuni in some flocks of waterfowl (e.g. Sandhill Cranes [Lu et al., 2013]), versus largely absent in others (e.g. California Gull [Lu et al., 2011]).
Waterborne Campylobacter spp. are likely to originate from recent fecal contamination of water by waterfowl and farm animal manure runoff, in addition to discharges of poorly or non-disinfected sewage effluent or septic seepage (Koenraad et al., 1994; Obiri-Danso and Jones, 1999; Abulreesh et al., 2006; Kuusi et al., 2005; Jokinen et al., 2010; Hellein et al., 2011). River and lake water have several potential contamination sources such as cattle and sheep on pasture and manure spreading on fields within watersheds, direct fecal contamination by wild birds and animals, human untreated waste in some regions and treated municipal wastewater (Figure 1). The relative importance of different sources and extent of contamination is highly dependent upon the hydrogeology of the watershed. While farming and urban areas are important sources, remote regions may still have Campylobacter contamination due to wild animals. Also, bacterial discharge from farmland to waterways is highly dependent on rain/snow events that mobilize fecal deposits (Muirhead et al., 2006; Ferguson et al., 2010). Humans may also acquire campylobacteriosis from natural water by bathing, recreation/canoeing, or drinking directly from within the watershed.
Campylobacter infection is an acute self-limited gastrointestinal illness with an incubation period that is longer than most other intestinal infections: commonly two to five days but up seven days have been reported. The mean incubation period is 3.2 days ranging approximately from 1 to 10 days (Blaser, 1997; Feodoroff et al., 2010; Nichols et al., 2012).
Patients shed high numbers of C. jejuni in voided material during their symptomatic infection phase, which commonly last three to five days. Duration of shedding lasts from a few hours to three weeks (average 15 days) (Nichols et al., 2012; Feodoroff et al., 2010; Butzler, 2004). Limited data is available on the concentration in human feces, but in three patients’ concentrations varied from 6×106 to 109 CFU/g (Blaser and Wang, 1980). Nonetheless, human-to-human transmission of Campylobacter is uncommon (Blaser, 1997).
Campylobacter enteritis most frequently affects children aged < 4 years and the infection rate is higher in boys and adult males than in girls and adult females (Allos, 2001; Kotloff et al., 2013). The infection frequency displays a strong seasonal variation in temperate climates with infections being more common in summer than in winter (Nylen et al., 2002; Schönberg-Norio et al., 2004; Kovats et al., 2005). The reason for the summer peak of human infections remains unknown but it may be affected by the higher prevalence of sporadic foodborne infections together with higher probability of waterborne outbreaks in conjunction with summer activities, such as outdoor food handling practices and the use of non-community water supplies (Olson et al., 2008). The seasonal variation is less distinct in tropical and subtropical areas (Kovats et al., 2005) and fly transmission has been hypothesized as an explanatory factor (Nichols, 2005).
Antibodies to Campylobacter antigens are present for several months conferring a short-term immunity to the homologous strain (Black et al., 1992). In developed regions where infections are uncommon, population level immunity is usually low and active immunity after symptomatic infection disappears rapidly and does not provide protective immunity against non-homologous strains (Allos, 2001; Blaser, 1997). Occupational exposure (farmers, slaughterhouse workers etc.) may acquire immunity and may occasionally be asymptomatic shedders of campylobacters (Ellström et al., 2014). Epidemiological features of infections in low-income countries suggest that due to several infection episodes in childhood leading to acquired immunity, older persons rarely experience symptomatic infection but may shed the pathogen.
Hygienic food preparation needs high quality water in food production and related processing areas (for cleaning food handing surfaces and utensils, hands etc.). Further, availability for proper hand washing facilities, toilets and clean water are of primary importance for safe food production. The prevention of fecal contamination of drinking water and maintenance of a residual chlorine concentration in the distributed drinking water are critical control measures to reduce the numbers of waterborne Campylobacter infections in regions with centralized water supplies and distribution. Private wells should be protected from fecal contamination by constructing them in such a manner that any fecal contamination source is not close to well and surface water cannot contaminate the well, e.g. after heavy rain/flooding. Protection of raw water sources from fecal contamination is one of the first hygienic measures, promoting the production of drinking water in a way requiring less costly water treatment (http://www.who.int/water_sanitation_health/en/). Many cases of C. jejuni infections are associated with drinking water cross-connection with wastewater infrastructure (Pitkänen, 2013). The water safety plan (WSP) approach introduced by WHO is a risk management framework that supports the production of high quality drinking water worldwide with multiple benefits (Gunnarsdóttir et al., 2012).
Campylobacter detection methods have been developed since Campylobacter jejuni was first isolated from the feces of patients with gastrointestinal disease in the 1970s (Dekeyser et al., 1972) and include culture-based and direct molecular methods. Campylobacter species are fastidious bacteria that are oxygen sensitive and are grown in a microaerobic atmosphere containing 3 to 10% (v/v) oxygen and 5 to 10% (v/v) carbon dioxide (Kelly, 2001). Some species also require hydrogen for their growth. Colonies directly grown on solid media are usually incubated at 41.5°C with fecal samples that usually contain high numbers of viable Campylobacter cells (Jacobs-Reitsma et al., 2008; Ugarte-Ruiz et al., 2012). Thermotolerant Campylobacter can also be cultivated from feces or mixed environmental media with antimicrobial-containing selective media (blood-based or charcoal blood-free) under microaerophilic conditions at an elevated temperature (42°C). However, initial liquid enrichment is generally used before plating on solid selective media to promote the recovery of low numbers of cultivable Campylobacter cells from environmental samples (Hänninen et al., 2003; Jacobs-Reitsma et al., 2008; Kim et al., 2016). The selective agents most often used include cefoperazone, amphotericin B, trimethoprim and vancomycin, and the media also contain sterile sheep or horse blood, or charcoal to neutralize the toxic effects of oxygen and light (Jacobs-Reitsma et al., 2008; Kim et al., 2016).
Since cultivation of Campylobacter spp. requires specific conditions including microaerobic atmosphere, the isolation of Campylobacter spp. from water is rarely successful or attempted, and was only reported in eight out of the 29 outbreaks reviewed by Pitkänen (2013). Thus far, studies have shown that it is difficult to isolate Campylobacter spp. from water related to waterborne Campylobacter outbreaks mainly due to insufficient and delayed water sampling and analysis (Bopp et al., 2003; Hänninen et al., 2003; Jakopanec et al., 2008). Generally, failure to isolate Campylobacter spp. is due to deficiencies in the detection methods applied to water samples (Rollins and Colwell, 1986; Jacobs-Reitsma et al., 2008), i.e. insufficient sample volumes and selective culture (Miller and Mandrell, 2005). The current standard method for the detection of thermotolerant Campylobacter species from water is based on membrane filtration as an initial concentration step (ISO 17995, 2005), followed by liquid enrichment before plating onto a solid selective medium, so as to recover low numbers of Campylobacter cells usually existing in environmental samples (Hänninen et al., 2003, Jacobs-Reitsma et al., 2008; Ugarte-Ruiz et al., 2015). Enrichment using Bolton broth is the primary method used for isolation of Campylobacter spp. in drinking water (ISO 17995, 2005), and the use of increased sample volume is recommended even though it may require the use of larger diameter filters (Hijnen et al., 2000) than the conventional 47 mm in cases where the water under examination is turbid. Direct plating methods employed for stool samples are unsuitable for quantitative recovery of low numbers of Campylobacter spp. present in environmental samples (Rollins and Colwell, 1986, Hänninen et al., 2003), and in water with high microbial biomass, non-targeted bacterial groups may out-compete the growth of Campylobacter spp. during the enrichment step (Abulreesh et al., 2005). For sewage influent and effluent samples, the selectivity of the enrichment may be increased by use of Preston broth at an elevated temperature of 41.5°C instead of 37°C (Koenraad et al., 1995) and a 21 h enrichment time as compared to the standard time of 44 h (Pitkänen, 2013), or addition of a wider range of antimicrobial agents (Kim et al., 2016). Alternatively a filter method, where motile Campylobacter spp. move through the pores in membrane filter on unselective medium prior to incubation at the growth temperature, have been used for separation of Campylobacter spp. from the non-target bacteria (Diergaardt et al., 2004; Rechenburg and Kistemann, 2009).
Methods for species identification and strain typing are not matrix-dependent, i.e. any method available for Campylobacter typing may be utilized in further characterization of Campylobacter isolates. The traditional subtyping methods include phenotyping, serotyping, biotyping, and phage typing (Butzler, 2004). The minimum standard for identifying Campylobacter spp. includes colony morphology, Gram’s stain, motility, and an oxidase test. To separate C. jejuni from C. coli, a hippurate-hydrolysis test has traditionally been used, although there are also hippurate-negative C. jejuni (Totten et al., 1987).
More recently, a wide range of nucleic acid-based methods have been used to confirm presumptive Campylobacter isolates from media. Due to the biochemical inertness of Campylobacter spp., molecular methods such as PCR and sequencing of the 16S rRNA gene are now generally used to differentiate Campylobacter-species. However, the sequence variability in the 16S rRNA gene in C. jejuni and C. coli does not differentiate these species, necessitating the use of other gene targets of PCR and sequencing of the amplicon, for example, the hipO-gene (Linton et al., 1996) or groEL- and rpoB-gene (Kärenlampi et al., 2004; Korczak et al., 2006). Indeed, PCR methods targeted to hipO gene may provide a more accurate differentiation between C. jejuni and C. coli than the phenotypic hippurate test (Abu-Halaweh et al., 2005; Abulreesh et al., 2006; Jensen et al., 2005). In addition, matrix-assisted laser desorption ionization-time of flight mass spectrometry (MALDI-TOF MS) (Mandrell et al., 2005) and a number of genotyping methods, such as pulsed-field gel electrophoresis (PFGE), restriction fragment analysis of Campylobacter flagellin genes (fla-RFLP), amplified fragment length polymorphism (AFLP), MLST) and direct sequencing (Butzler, 2004; On et al., 2008; Wassenaar and Newell, 2000; Clark et al., 2003; Kovanen et al., 2014) can be used to aid in the identification of Campylobacter species.
Recently whole genome MLST (wgMLST) has been increasingly applied for studies of outbreak-associated C. jejuni isolates (Kovanen et al., 2016). A recent study using wgMLST of C. jejuni isolates from a waterborne outbreak revealed that sometimes pulsed-field gel electrophoresis (PFGE) may overestimate the clonal relationship between some of the apparent outbreak-related C. jejuni strains (Revez et al., 2014). It is possible that in previous years, when PFGE was solely utilized for genotyping of outbreak isolates, some unrelated, sporadic human cases were mistakenly classified as part of the waterborne outbreaks. The use of molecular tools such as wgMLST is increasing in outbreak investigations (Moffatt et al., 2016).
The reliance on conventional cultivation alone for Campylobacter spp. detection and subsequent subtyping is not practical, since viable but not culturable (VBNC) Campylobacter cells occur (Tholozan et al., 1999; Abulreesh et al., 2006; Bronowski et al., 2014; Oh et al., 2015). The coupling of PCR detection after enrichment to the culture-based method increases the work load but substantially shortens the time requirement for detection and confirmation of Campylobacter spp. (i.e. from two or more days down to five hours). The use of PCR after enrichment may reduce the presence of false negative analysis results in cases where the Campylobacter colonies are overgrown by the growth of non-target bacteria on a solid agar medium. Ideally quantitative real-time PCR for Campylobacter detection should been applied directly to water samples (Nogva et al., 2000; Yang et al., 2003; Nam et al., 2005; VanDyke et al., 2010; Clark et al., 2011; Park et al., 2011). These studies have utilized Campylobacter PCR assays targeting the 16S rRNA gene (Bang et al., 2002; Moreno et al., 2003; Josefsen et al., 2004; Hellein et al., 2011), the 23S rRNA gene (Engvall et al., 2002), 16S-23S rDNA internal transcribed (ITS) region (Khan and Edge, 2007) and the flagellin genes flaA and flaB (Waage et al., 1999; Moore et al., 2001). Other molecular assays reported have targeted genes such as glyA (Jensen et al., 2005), gafF and ceuE (Nayak et al., 2005; Hellein et al., 2011), ORF-C sequence (Sails et al., 2003) and cpn60 gene (Banihashemi et al., 2012).
However, the problem of detecting both viable and non-viable cells has so far restricted applications of PCR techniques. Therefore, techniques differentiating living from dead cells have been studied and may well provide novel tools for rapid and accurate detection of viable microbes (Cenciarini-Borde et al., 2009; Fittipaldi et al., 2012; Pitkänen et al., 2013). For example, it has been suggested that RT-qPCR assay based Campylobacter spp. specific rRNA signals are associated to active bacterial populations in environmental waters since they were in better agreement with the culture-based results of thermotolerant Campylobacter spp. than that of rDNA-based assays (Pitkänen et al., 2013). Novel molecular platforms such as isothermal amplification techniques and high-throughput sequencing approaches may provide new possibilities for Campylobacter spp. detection. Isothermal amplification coupled with microarrays provide opportunity to simultaneously study a large number of microbial targets, including genes of C. jejuni in less than 20 minutes (Tourlousse et al., 2012).
Most warm-blooded animals are asymptomatic carriers of Campylobacter spp. The presence of Campylobacter spp. in mammal and bird feces: cat, dog, cow, seagull, chicken, duck, geese and pigs is commonly reported (Hellein et al., 2011). For example, in Canada, the presence of Campylobacter spp. was shown in a total of 37 animal fecal samples (35.6%) out of 104 samples collected from goat, cow, chicken, goose, duck and pig feces (Jokinen et al., 2010). However, Campylobacter spp. was absent from rabbit and rat feces and present in less than 15% of horse, dog, llama, alpaca and sheep fecal samples (n=113; Jokinen et al., 2010). In Queensland, Australia, 24 out of 40 possum fecal samples (60%) contained 2.0×105 to 2.0×107Campylobacter spp. cells/g (Ahmed et al., 2012). In the same study, 24% of bird fecal samples had 6.6×104 to 6.6×106Campylobacter spp. cells/g (n=38). Noting that the presence of animal Campylobacter spp. does not mean they are infectious in humans, strain typing is necessary (e.g. Mughini Gras et al., 2013).
Sewage is a major source of Campylobacter spp. in the environment. Septic seepage into well waters and cross-connections between sewerage and drinking water systems have caused several waterborne outbreaks (Pitkänen, 2013). Non-disinfected wastewater effluents discharge Campylobacter spp. to environmental waters (Lauria-Filgueiras and Hofer, 1998; Hokajärvi et al., 2013; Rechenburg and Kistemann, 2009). Table 2 summarizes the reported Campylobacter spp. numbers in raw sewage and wastewater treatment plant effluents from developed regions.
Table 2 summarizes the published reports of Campylobacter spp. numbers in sludge. For example, at sewage treatment plants in Sweden, 20.3% (13/64) and 9.4% (6/64) of raw sludge samples contained viable C. jejuni and C. coli, respectively, whereas only 2.9% (2/69) and 1.4% (1/69) of treated sludge samples were C. jejuni and C. coli positive (Sahlström et al., 2004).
Because C. jejuni and C. coli commonly colonize a large numbers of animal hosts, their presence in fresh fecal material is common. For example, 100% presence of Campylobacter spp. in poultry wastewater (n=13; geometric mean 6.0×106 MPN/L) and in pig slurries (n=6; geometric mean 4.9×106 MPN/L) in Mediterranean area has been reported (Rodríguez and Araujo, 2010). Origin of manure, the manure treatment process, climate and other environmental factors play a role in the survival and numbers of Campylobacter spp. in manure and after spreading to land (Nicholson et al., 2005).
Campylobacter spp. are frequently isolated from fresh surface waters (Stelzer and Jacob, 1991; Koenraad et al., 1997; Jones 2001; Savill et al., 2001; Diergaardt et al., 2004; Hörman et al., 2004; Vereen et al., 2007; Hellein et al., 2011; Jokinen, et al., 2012; Hokajärvi et al., 2013). Table 3 summarizes the published studies reporting the detection of Campylobacter spp. and available Campylobacter spp. counts in surface waters. The high variability in the reported detection rates and counts of Campylobacter spp. in surface water is in part due to the different methods used for detecting Campylobacter spp. from water. For example, the Campylobacter counts have been analyzed by direct plating (Vereen et al., 2007), using Campylobacter spp. specific quantitative PCR methods (Hellein et al., 2011; Van Dyke et al, 2010) and by semi-quantitative enrichment method (Hokajärvi et al., 2013; Diergaardt et al., 2004) – making comparison between studies rather pointless given the different forms (dead or culturable) reported. Campylobacter spp. counts also naturally vary, due to processes that mobilize them off surfaces and their dilution within surface waters (Sterk et al., 2016).
Noting the bias of culture methods to detect C. jejuni and C. coli, C. jejuni has been the species identified most frequently from surface waters (Thomas et al., 1999a), yet C. coli and C. lari are also commonly reported (Thomas et al., 1999a; Denis et al., 2011 Hokajärvi et al., 2013), associate with the presence of agricultural runoff or large flocks of waterfowl (Bolton et al., 1987; Obiri-Danso and Jones, 1999). In a study in Ontario, Canada, 73% of isolates from the samples of waterfowl feces (n=15 out of a total of 52 samples) were identified as C. jejuni, 13% were C. coli and 27% C. lari (Van Dyke et al., 2010). By using gene detection after enrichment, it has been noted that the variety of Campylobacter species in watersheds is even broader, including C. consicus, C. gracilis, C. hyointestinalis, C. helveticus among others in addition to C. jejuni, C. coli and C. lari detected using culturing (Table 4) (Tambalo et al., 2016).
Campylobacter spp. are absent in groundwater not influenced by surface water, but many groundwaters may be contaminated during events, such as after flooding, hence the general need for disinfection. The majority of the Campylobacter outbreaks have been linked to relatively small groundwater works without adequate disinfection (Pitkänen, 2013; Guzman-Herrador et al., 2015). In some regions the occurrence of Campylobacter spp. in groundwater may be continuous as reported from wells in Canterbury, New Zealand, where Campylobacter spp. was detected in 12% (16/135) of the wells associated with intensive dairying combined with border strip irrigation, of which 11 samples out of 135 contained C. jejuni (8.1%) and the Campylobacter counts varied from <0.6 to 3.1 MPN/ L (Close et al., 2008). In another study from shallow groundwater aquifers in New Zealand, low counts of Campylobacter spp. were detected in 75% of samples (n=18; Savill et al., 2001).
The contribution of drinking water to the burden of sporadic Campylobacter infections may be significantly underestimated. It is particularly difficult to recognize the association with water when private wells and untreated surface water is used as drinking water (Kapperud et al., 2003; Schönberg-Norio et al., 2004; Olson et al., 2008). For example, in Norway (Brennhovd et al., 1992) and Finland (Pitkänen et al., 2015), no Campylobacter spp. were recovered from water samples, but this is not always the case. Positive recoveries have been reported for Northern Ireland, 2.2% (2/91) drinking water from domestic household taps were PCR positive for Campylobacter spp. (Moore et al., 2001), and in New Zealand, 29.2% (7/24) of drinking water samples from centralized water supply were reported to be Campylobacter spp. positive (Savill et al., 2001). Also, 21% (5/24) of household taps fed from rainwater tanks in Southeast Queensland, Australia contained 5.0 to 1.0×102 Campylobacter cells/L when assayed as 16S rRNA gene copies (Ahmed et al., 2012). In all of these detections, however, the infection risk to the public is only of potential concern as the Campylobacter counts detected were presumably low, not necessarily viable cells nor genotypes of human-infective species, like C. lari (Savill et al., 2001).
C. jejuni has also been detected in 2% of the sea water samples examined in Greece (n=200) and represented the only Campylobacter species identified in the study (Arvanitidou et al., 1995). In Catalonia, Spain, Campylobacter spp. were absent from seawater samples (n=8) but Campylobacter spp. numbers below 5.0×102 MPN/L were detected in 78% of marsh water samples (n=9) from the same area (Rodriguez and Araujo, 2010). In Northern Ireland, Campylobacter spp. was absent from seawater samples (n=6) but were detected using a PCR method in 4.3% of the estuary lough water samples from protected bays (n=23; Moore et al., 2001). The presence of Campylobacter spp. is clearly sampling site dependent, as was seen in a Polish study where Campylobacter spp. were confirmed in 19.7% of the river water sampling sites nearby the contamination sources, but only 5.6% (3/54) of the lagoon and none of the 20 marine bay water samples (Daczkowska-Kozon and Brzostek-Nowakowska, 2001). The formation of VBNC cells in the saline environments may contribute to the low prevalence of Campylobacter spp. in seawater, when culture-based detection is used (Jackson et al., 2009; Gin and Goh, 2013).
Manure spreading operations are known to spread Campylobacter spp. to agricultural fields, and grazing livestock deposit Campylobacter spp. in their manure on pastures (Brown et al., 2004). The extent of wildlife feces in spreading Campylobacter spp. into terrestrial forest soils is less known.
Intertidal sediments are known reservoirs of Campylobacter spp. as reported from EU bathing sites in North West England where urease positive thermophilic campylobacters (UPTC) and C. lari were detected (Obiri-Danso et al., 2001).
Campylobacter spp. are commonly present in natural water systems (rivers, lakes, ponds) and their presence needs to be considered when natural water is used for irrigation (for occurrence in environmental water see Section 2.2.5) (Banting et al., 2016; Gu et al., 2013).
Agricultural application of raw sludge or anaerobically digested biosolids to arable land has long been recognized as a Campylobacter source to horticultural produce (Koenraad, 1997; Park and Sanders, 1992).
There are no reports about Campylobacter spp. in fish, but shellfish harvested from fecally contaminated waters frequently contain Campylobacter spp. (Wilson and Moore, 1996). However, in the Campylobacter-positive shellfish samples, most were other species than the common human pathogens (C. jejuni or C. coli), such as C. lari variants (Debruyne et al., 2009).
Airborne transmission of campylobacteriosis is not considered significant for Campylobacter spp., which are oxygen intolerant bacteria causing infection through the fecal-oral route. However, flies are common carriers of Campylobacter spp. especially in conditions where sanitation and excreta disposal is underdeveloped (Khalil et al., 1994).
Campylobacter spp. isolated from the environment are likely to have originated from fresh fecal material. Campylobacter spp. are not expected to regrow in the environment since they are considered unable to multiply outside the intestines of warm-blooded host animals and birds (Jones, 2001). Nonetheless, laboratory studies indicate the potential for C. jejuni to grow within soil/water amoebae (reviewed within Vaerewijck et al., 2014). C. jejuni survives at 4°C in moist, sun-sheltered environments (Bolton et al., 1987; Obiri-Danso and Jones, 1999; Kärenlampi and Hänninen, 2004), but is readily killed by temperatures reached in pasteurization, cooking, and frying (Habib et al., 2010). Under UK field conditions Campylobacter spp. survives in livestock manure slurries for 32 days, but only 2 to 4 days in solid manure heaps in temperatures greater that 55°C (Nicholson et al., 2005). Maximum survival periods following the land spreading of manure and slurry varied from four days to the more than 32 days with some indication of longer survival in clay loam grassland than in sandy arable soil (Nicholson et al., 2005). An in vitro study also showed that the survival of C. coli in swine manure was for at least 25 days at + 4°C but decreased to a few days at +22°C (Bui et al., 2011).
Table 5, Appendix A and Appendix B summarize the available Campylobacter spp. persistence data in different water matrices. Different survival characteristics of the Campylobacter spp. under environmental conditions may influence the diversity of different campylobacters (Korhonen and Martikainen 1991; Thomas et al., 1999b). For example, C. lari can survive better in aquatic environments than C. jejuni and C. coli (Obiri-Danso et al., 2001), and culturable C. jejuni survive longer than C. coli in lake water (Korhonen and Martikainen, 1991). Furthermore, C. coli and C. upsaliensis have demonstrated comparable survival characteristics (Thomas et al., 1999b).
Campylobacter spp. do not carry many of the classic stress response mechanisms, but still employ a number of strategies enabling it to survive in the environment (Bronowski et al., 2014). However, the Campylobacter survival mechanisms in the environment are poorly understood and more data to predict the survival characteristics of Campylobacter spp. in water is needed (Gonzalez and Hänninen, 2012). The mechanisms may differ from those for most of the other enteric bacteria (Murphy et al., 2006). As with other enterics, C. jejuni enter into VBNC state under unfavorable conditions, however, what is different is that the size of cells is often reduced; with the shape of cells transformed from helical rods to cocci (Rollins and Colwell 1986; Jones 2001; Oliver 2005). In a recent study C. jejuni maintained the ability to adhere to intestinal cells after three weeks incubation in freshwater at 4°C indicating that the VBNC forms may retain their infectivity (Patrone et al., 2013). In artificial sea water at 4°C, C. jejuni strains survived in the VBNC form through a period lasting from 138 to 152 days (Baffone et al., 2006). In drinking water at 4°C, the origin of the strain and the culture conditions were an important factor determining campylobacter survival (Cools et al., 2003).
The key factors affecting the survival of Campylobacter spp. in aquatic environments include temperature, light, biotic interactions and concentrations of oxygen and nutrients (Thomas et al., 1999b). The survival of campylobacters is favoured by low temperature and the absence of sunlight as shown in the inactivation rate studied conducted in Catalonia, Spain (Rodríguez and Araujo 2012). Not only were campylobacters more susceptible to high light intensities than other enteric bacteria, but they appear to be unable to repair damage to DNA (Jones 2001). It has been reported that low numbers of indigenous microbiota favor the culturable detection of stressed Campylobacter cells (Korhonen and Martikainen, 1991). However, the viability of Campylobacter spp. in water systems is favoured by biofilms (Svensson et al., 2008) and by free-living amoebae harboring bacteria intracellularly (Snelling et al., 2005). The presence of protozoan grazers such as Acanthamoeba spp. has been reported to increase the survival of C. jejuni in vitro studies in water (Axelsson-Olsson et al., 2005).
Overall, very little comparative data was available to identify surrogates for campylobacter inactivation by different sanitation management systems. Nonetheless, based on what is understood and summarized above (and in the chapter Using indicators to assess microbial treatment and disinfection efficacy), E. coli, enterococci and other fecal indicators may be reasonable surrogates. What is understood for campylobacters by sanitation systems is summarized below. In general, the absence of fecal indicator bacteria can be considered as a reliable proof of absence of Campylobacter spp. after the sanitation treatments. In oxygen-rich processes, Campylobacter spp. are presumably less persistent than fecal indicator bacteria. On the contrary, in anaerobic processes, the survival of Campylobacter spp. might be even better than fecal indicator bacteria (see section 3.1.5) and must be taken into consideration when evaluating the treatment efficiency.
Campylobacter spp. might be present in effluents from on-site sand filters as shown by Kauppinen et al. (2014). The exact removal rates, however, remain unknown due to the semi-quantitative nature of the Campylobacter detection method and the inconsistent presence of Campylobacter spp. in the influent water.
Only little is known about Campylobacter spp. reductions by storage of human fecal material, but it is assumed survival would be similar as seen for animal manures. It is likely that Campylobacter survival in fecal material is dependent on available water (aw), as reported in studies related to foodstuffs (Fernandez et al., 1985). While other food processing pathogens have a number of mechanisms to withstand stresses (Burgess et al., 2016), Campylobacter spp. are considered uniquely sensitive to a number of environmental conditions and are generally less able to tolerate environmental stress than other foodborne pathogens (Park, 2002).
In experiments with swine manure in Denmark, C. coli remained viable for up to 24 days at 4°C, based on both culture and RT-qPCR results (Bui et al., 2011). Survival in swine feces was dependent on storage temperature, surviving one week at 15°C but only a few hours at 42°C. Hence, Bui et al. (2011) suggests simply treated feces to temperature up to 42°C or even hotter for few hours before application on the agricultural soil to inactivate campylobacters; such as through solarization treatment (Simmons et al., 2013).
Potential pathogen content of urine is low compared to feces (Höglund et al., 2002). For example, in a study of pathogens in source-diverted urine in South Africa, no Campylobacter was not detected in any of the urine samples (Bischel et al., 2015). Urine diversion enhances the dehydration of separately stored feces and thus, the aw decrease in the fecal material may result in a higher reduction in Campylobacter spp. numbers in dry toilets using urine diversion compared to combined systems.
Temperature and oxygen-content are considered major factors influencing Campylobacter spp. inactivation during sludge and manure composting, yet only limited data on reductions are available. For example, in France, aerated composting containing thermophilic phase (50 to 65°C) reduced the C. jejuni gene copy numbers from approximate 1.0×105 copies/g level to non-detect (Wery et al., 2008). In a pen manure (20 to 50°C) in Australia, the numbers of C. jejuni gene copies declined below the detection limit within one week (Klein et al., 2011), but a windrow compost configuration was not able to inactivate culturable C. coli from the sewage sludge in Sweden (Sahlström et al., 2004), possible due to uneven heating and poor mixing during the composting process.
The low infectious dose of C. jejuni and its demonstrated ability to survive in the top 5 cm of soils for at least 25 days at 10°C must be noted prior to any reuse of solids that contain fecal matter (Ross & Donnison, 2006). As a residual management strategies, the stockpiling of livestock bedding waste from animal pens to a secondary store, and storing them under conditions conducive for increased temperature is considered a simple and cost-effective treatment for rapidly lowering levels of zoonotic agents, including Campylobacter spp. in solid farm wastes (Hutchison et al., 2005).
When Sheludchenko et al. (2016) studied fecal microbes in remote and rural maturation ponds in Australia, they reported baffled maturation ponds operated more effectively for removal of presumptive Campylobacter spp. than other waste stabilization pond systems; as you would expect based on improved residence time control and reduced turbidity. In clear waters, rapid sunlight inactivation or at least the loss of culturability of C. jejuni is possible as detected in a survival study where waste stabilization pond effluent in seawater and river water was tested in New Zealand (Sinton et al., 2007).
The efficiency of aerated lagoons to remove Campylobacter spp. remains unknown. Of other enteric bacteria in aerated wastewater lagoons, Salmonella reduction of approximately 0.91 log10 and fecal coliform reduction of 1.4 log10 has been reported in Tunisia (Ellouze et al., 2009). However, it is not known if these numbers are indicative for Campylobacter spp. reduction.
The VBNC state of C. jejuni cells, which are of a coccoid form, can be induced under oxygen-rich aerobic conditions (Oh et al., 2015). Thus, the ability of microaerophilic Campylobacter spp. to survive in aerated conditions may impact on Campylobacter spp. viability yet be missed if culture-based methods are used. However, the decimal reduction of C. jejuni HipO gene has been shown to be significantly faster in aerobic conditions as compared to anaerobic conditions in studies of thermophilic bio-waste sludge treatment in Austria (Wagner et al., 2009).
In addition to the oxygen content, also temperature affects Campylobacter culturability. This was seen for example in anaerobic swine manure lagoon samples in Mississippi, USA, where the rising lagoon water temperature was found to decrease viable Campylobacter counts (McLaughlin et al., 2012).
UK data demonstrated that wetlands constructed as horizontal reed beds may remove approximately 3 log10 of the Campylobacter spp. from poultry manure wastewater (Duggan et al., 2001). While sequential and continuous loading had little effect on Campylobacter removal, a rising water level seemed to leach Campylobacter from the reed beds back into the effluent (Duggan et al., 2001). In Germany, Alexandrino et al. (2007) used qualitative PCR assay targeting C. jejuni, but non-detects for treating primary sewage by vertical and horizontal subsurface flow constructed wetlands hampered their estimate of removals.
As a common cause of gastroenteritis worldwide, Campylobacter spp. are often present in high numbers in untreated sewage (Table 2). While wastewater treatment generally reduces the number of campylobacters, combined sewer overflows (CSO) release untreated sewage to the receiving surface waters. It has been reported that during and after heavy rainfall when CSO is discharged, the rivers become highly contaminated with Campylobacter spp. and other kinds of pathogens (Rechenburg and Kistemann, 2009).
Even though Campylobacter cells are reduced by aerobic, biological treatment of wastewater, these processes do not completely eliminate Campylobacter spp. (Koenraad et al., 1997).
Trickling filters have been reported to reduce the Campylobacter counts (Table 6; Arimi et al., 1988; Rechenburg and Kistemann, 2009), yet in other studies, only minimal reduction has been reported (Table 6; Koenraad et al., 1994); thus large numbers of Campylobacter spp. might be released into the environment daily from sewage treatment plants if no other treatment is used.
In studies from late 1980’s, more than 0.8 log10 reduction of culturable Campylobacter in secondary treatment (including the activated sludge process) were reported (Table 6; Höller, 1988; Stelzer and Jacob, 1991; Stampi et al., 1992; Koenraad et al., 1994).
More recent reports, often based on molecular detection of Campylobacter spp., show discrepancies in reduction and indicate the enhanced ability of this genus to persist and survive in different environments (as reviewed in Whiley et al., 2013). For example, Wéry et al. (2008) study in France using qPCR, concluded that C. jejuni VP1 gene survived better during the activated sludge treatment compared to the E. coli lacZ gene. However, due to the lower copy number in the influent, they did not detect C. jejuni gene copies in the treated water while the E. coli genes were still quantifiable.
No reports of Campylobacter spp. reduction by oxidation ditches were identified. It is presumable that the successful oxidation improves Campylobacter reduction. See discussion about the effect of oxygen-rich conditions on Campylobacter spp. viability in section 188.8.131.52 (aerated lagoons).
In studies reviewed by Hai et al. (2014), almost complete removal of bacteria by membrane bioreactors (MBR) was reported, whereas virus removal was inconsistent. Even though Campylobacter was not mentioned, it is presumable that a well-functioning MBR system is efficient in removing Campylobacter.
Whiley et al. (2013) suggested in their review that oxygen intolerant Campylobacter spp. might survive even better than traditional fecal indicator bacteria during anaerobic digestion. Indeed, it has been observed that C. jejuni survives in a viable and culturable state during mesophilic anaerobic digestion (35°C) and the estimated time required for 1 log10 reduction was 793 days under those conditions (Kearney et al. 1993). Also in a study by Koenraad et al. (1994), campylobacters were isolated from 88% of secondary biosolids, with an average count 2.5×103 MPN/L (n=30). Horan et al. (2004), using a culture-based methodology, observed no inactivation of C. jejuni within 22 days at 35°C in a primary sludge digester and only 0.4 log10 reduction was observed after the secondary sludge digestion at 15°C for 14 days. Hence, anaerobic digestion appears to be a relatively poor treatment approach to reduce campylobacter numbers.
However, treatment conditions have a major impact on Campylobacter spp. reductions. The absence of campylobacters was noted when biosolids are digested aerobically (Betaieb and Jones, 1990; Stelzer and Jacob, 1991) and many reports have indicated that culturable Campylobacter spp. in sludge are eliminated by digestion processes (Jones et al., 1990; Stampi et al., 1999). In a Swedish study in 2000 to 2001, thermophilic anaerobic digestion at 55°C, mesophilic anaerobic digestion at 34 to 42°C, composting and sedimentation all seem to remove Campylobacter spp. from sewage sludge (Sahlström et al., 2004). The sanitation of sludge using composting was also demonstrated in a study from France, where the thermophilic phase of composting was capable of reducing the C. jejuni VP1 gene copy numbers from 3.9×105/g of compost wet weight to non-detectible (Wery et al., 2008).
After the digestion of dewatered biosolids, storage temperature plays an important role in further reducting Campylobacter spp. Ahmed and Sorensen (1995) reported more than 4 log10 reduction of culturable C. jejuni counts within a day at 50°C while only 2 log10 reduction was observed within 62 days at 5°C.
When further removal of campylobacters is required to minimize human exposure, i.e. for wastewater reuse purposes, in close proximity of recreational areas or raw water intake sites for drinking water production (Levantesi et al., 2010), then various tertiary wastewater treatments options should be considered, as introduced below.
The use of PIX (FeCl3) and PAX (AlCl3) coagulants was shown to efficiently reduce the microbial load in wastewater effluents in Finland (Pradhan et al., 2013). However, the reduction of Campylobacter spp. was not evaluated due to non-detects in the secondary treated influent.
Slow sand filtration has long been used for drinking water purification. The removal efficiency of slow sand filtration has been studied at full-scale drinking waterworks in The Netherlands, where 3.4 ± 0.6 log10 reduction of Campylobacter spp. was reported (Hijnen et al., 2004).The culture counts of Campylobacter spp. may reduce in sand filtration more efficiently than E. coli counts (Hijnen et al., 2004). Sand filtration has more recently been used as a tertiary treatment option (Rechenburg and Kistemann, 2009), however, no campylobacter removal rates for this unit process for wastewater were identified.
Microfiltration with a nominal porosity of 0.1 micron (meaning there are larger pores present but poorly defined) has a moderate efficacy in removing Campylobacter spp., while ultrafiltration and nanofiltration filters (with less than 0.05 micron pore sizes) as well as reverse osmosis are expected to provide very high removals of Campylobacter spp. (http://www.cdc.gov/healthywater/drinking/home-water-treatment/household_water_ treatment.html, accessed 29th June 2016). For example in Belgium, the ultrafiltration permeate contained no fecal bacteria (Levantesi et al., 2010). The real concern is with absolute membrane removal processes is the day-to-day performance, or ability to maintain integrity (see chapter Sewered System Technologies).
No research reports were identified for these types of media. However, it is expected that Campylobacter spp. reductions in mono, dual and tri media follow the patterns observed using fecal indicator bacteria, especially E. coli.
Managed aquifer recharge (MAR) with treated municipal wastewater is used for water storage and additional purification in water reuse processes. Levantesi et al. (2010) studied the counts of fecal indicators in MAR processes at three European sites. The aquifer characteristics and the quality of the injectant water both appear to affect the quality of recovered water. It is presumable that Campylobacter spp. are reduced while the water passes through the soil at least with the same efficiency as E. coli , but no data was identified to confirm this.
Chemical disinfectants are applied at a concentration for a specified time to deliver what is known as the Ct (concentration x time), but many reports identified only provided concentration data. For example, tertiary treatment (disinfection) of treated wastewater at 1 to 3 mg/ L free chlorine was shown to reduce Campylobacter spp. counts below the culture method detection limit (Table 6; Stampi et al., 1992; Stampi et al., 1993; Koenraad et al., 1994). Based on the plate counting of bacteria, C. jejuni is generally considered more susceptible to chlorine than E. coli and thus the elimination of E. coli is considered adequate measure to confirm the absence of C. jejuni (Blaser et al., 1986). However, some caution is needed as it is well known that culture methods may seriously underestimate the C. jejuni (and E. coli) viable counts in chlorinated waters (Lehtola et al., 2006) and viable bacteria cells may remain inside protozoa under chlorine exposure (Snelling et al., 2005).
Alternative options to chlorine have been searched to fulfill the requirement of post-primary treatment disinfection without the hazards related to disinfection by-products. For example, peracetic acid disinfection (PAA; 3 mg/ L) after dissolved air flotation treatment have been shown to reduce the culturable Campylobacter spp. counts in wastewater effluent to below the detection limit (Pradhan et al., 2013).
UV disinfection can be effective against all waterborne pathogens if turbidity is sufficiently low (Hijnen et al., 2006). C. jejuni is considered more sensitive to UV compared to E. coli and the culturable cells of C. jejuni can be easily removed from water using UV. In clear waters (in sterile distilled water) at room temperature and when the occurrence of VBNC cells were not considered, a 3 log10 C. jejuni reduction may be been achieved with a fluence of 1.8 mJ cm-2 (Butler et al., 1987). The estimated required fluence for 4 log10 reduction of Campylobacter spp. is 14 mJ cm-2 (Hijnen et al., 2006). However, lower quality of the secondary effluent turbidity may hamper the efficiency of tertiary UV treatment at wastewater purification plants. Synergistic effects of PAA or H2O2 induced radical formation together with UV have been studied to achieve higher disinfection efficiency with more turbid wastewaters (Koivunen and Tanski, 2005).
It has been reported in purified (distilled) water that about two minutes under conditions of strong natural sunlight is enough for 1 log10 reduction of C. jejuni plate counts (Boyle et al., 2008). In sanitation applications, the true reductions of viable Campylobacter spp. are presumably somewhat lower mainly due to the occurrence of VBNC cells and differential light penetration properties in wastewater-impacted natural waters. In fresh surface water contaminated by sewage effluent, a 1 log10 reduction in C. jejuni took more than 82 h in the dark at 14°C, while the same reduction was achieved in 1 to 2 hours in sunlight (Sinton et al., 2007).
In experimental dessication conditions, Campylobacter strains remained viable for 2 to 10 h (Fernandez et al., 1985). Based on studies in feces on pasture, temperature and diffused oxygen, rather than desiccation increased the inactivation of Campylobacter spp. (Sinton et al., 2007).