SciELO - Scientific Electronic Library Online

vol.7 número3Resistencia a antibióticosb-lactámicos en Aeromonas hydrophila aislados de truchas arco iris (Oncorhynchus mykiss)Características funcionales del bacterioplancton cultivable de ambientes marinos y de estuario índice de autoresíndice de materiabúsqueda de artículos
Home Pagelista alfabética de revistas  

Servicios Personalizados




Links relacionados

  • En proceso de indezaciónCitado por Google
  • No hay articulos similaresSimilares en SciELO
  • En proceso de indezaciónSimilares en Google


International Microbiology

versión impresa ISSN 1139-6709

INT. MICROBIOL. vol.7 no.3  sep. 2004






Angela M. S. Cardonha1
Regine H. S. F. Vieira2*
Dália P. Rodrigues3
Andrew Macrae4
Gizele Peirano3
Grace N. D. Teophilo3

1 Department of Nutrition, PGCS, Federal Univ. of Rio Grande do Norte, RN, Brazil
2 Institute of Marine Sciences, Federal University of Ceará, Fortaleza, CE, Brazil
3 Fundação Oswaldo Cruz, Rio
de Janeiro, RJ, Brazil
4 Institute of Microbiology Prof. Paulo de Goes, Federal University of Rio de Janeiro, RJ, Brazil

Fecal pollution in water from storm sewers and adjacent seashores in Natal, Rio Grande do Norte, Brazil


Summary. A study on the distribution patterns of enteropathogenic bacteria polluting the shoreline in Natal, Rio Grande do Norte, Brazil, was carried out based on 72 samples obtained from three storm sewers and adjoining beach locations, Praia do Meio (PM), Areia Preta (AP) and Ponta Negra (PN). From each location, 12 water samples were taken and analyzed for fecal coliforms (FC) and Escherichia coli. In AP, two (16.7%) of the seawater samples and five (41.7%) of the storm sewer samples yielded values above 1.1 × 107 FC/100 ml, whereas only one (8.3%) of the samples from PM reached this level. There was no correlation (p > 0.05) between rainfall indeces and FC values. A total of 64 E. coli isolates were obtained: 37 from the storm sewer samples and 27 from the seawater samples. Of these isolates, four (O143, two O112ac, and O124) were enteroinvasive and two (O111 and O125) were enteropathogenic. Resistance to antibiotics and to heavy metals was also analyzed. Almost 36% of the E. coli strains isolated were resistant to more than one antibiotic. All strains were resistant to zinc and copper at the highest concentration tested (250 µg/ml), and several (23.4%) were resistant to mercury at 50 µg/ml. Our results agreed with previous reports that antibiotic resistance is commonly associated with heavy-metal resistance in pathogens. [Int Microbiol 2004; 7(3):213-218]

Key words: storm sewers · fecal contamination · heavy metals · antibiotic resistance

Received 7 February 2004
Accepted 2 April 2004


*Corresponding author:
R.H.S.F. Vieira
Instituto Ciências do Mar
Universidade Federal de Ceará
CEP 60165-082 Fortaleza, CE, Brazil
Tel. +55-852426422. Fax +55-852428355


Contaminación fecal en el agua de colectores pluviales y en la costa adyacente en Natal (Rio Grande do Norte, Brasil)

Resumen. Se realizó un estudio sobre la distribución de las bacterias enteropatógenas que contaminan la costa en Natal (Rio Grande do Norte, Brasil), a partir de 72 muestras obtenidas en tres colectores pluviales (storm sewers) y en unas playas adyacentes a los mismos, Praia do Meio (PM), Areia Preta (AP) y Ponta Negra (PN). En cada punto se tomaron 12 muestras, que se analizaron en busca de coliformes fecales (CF) y de Escherichia coli. En AP, dos (16,7%) de las muestras de agua de mar y cinco (41,7%) de las de agua del colector dieron valores superiores a 1,1 × 107 CF/100 ml, mientras que sólo una (8,3%) de las muestras de PM alcanzó este nivel. No se encontró correlación (p > 0,05) entre los índices de pluviosidad y los valores de CF. Se obtuvo un total de 64 aislados de E. coli: 37 a partir de muestras de colectores y 27 a partir de muestras de agua de mar. De estos aislados, cuatro (un O143, dos O112ac y un O124) eran enteroinvasivos y dos (O111 y O125) eran enteropatógenos. Se analizó también la resistencia a antibióticos y a metales pesados. Casi el 36% de las cepas de E. coli aisladas eran resistentes a más de un antibiótico. Todas las cepas eran resistentes al zinc y al cobre a la mayor concentración probada (250 µg/ml), y varias cepas (23.4%) eran resistentes al mercurio a 50 µg/ml. Nuestros resultados coinciden con trabajos anteriores que indican que en bacterias patógenas la resistencia a antibióticos suele ir asociada a la resistencia a metales pesados. [Int Microbiol 2004; 7(3):213-218]

Palabras clave: colectores pluviales · contaminación fecal · metales pesados · resistencia a antibióticos


Poluição fecal em águas de galerias pluviais e áreas adjacentes em Natal (Rio Grande do Norte, Brasil)

Resumo. Foi realizado um estudo sobre a distribuição de bactérias enteropatogênicas que contaminam a costa de Natal (Rio Grande do Norte, Brasil) a partir de 72 amostras obtidas em três galerias pluviais (storm sewers) e nas praias adjacentes às mesmas: Praia do Meio (PM), Areia Preta(AP) e Ponta Negra (PN). Em cada ponto foram tomadas 12 amostras nas quais foram investigadas a presença de coliformes fecais (CF) e Escherichia coli. Na AP duas (16,7%) das amostras de água do mar e cinco (41,7%) das águas das galerias apresentaram valores superiores a 1,1 × 107 CF/100 ml enquanto somente uma (8,3%) das amostras da PM alcançou este nível. Não foi encontrada correlação (p > 0,05) entre os índices pluviométricos e os valores de CF. Obteve-se um total de 64 isolados de E. coli: 37 a partir de amostras das galerias e 27 a partir de amostras de água do mar. Destes isolados, quatro (um O143, dois O112ac e um O124) eram enteroinvasivos e dois (O111 e O125) eram enteropatógenos. Foi analisada também a resistência a antibióticos e a metais pesados. Quase 36% das cepas de E. coli isoladas eram resistentes a mais de um antibiótico. Todas as cepas eram resistentes a zinco e a cobre na maior concentração testada (250 µg/ml), e várias cepas (23.4%) eram resistentes a mercúrio (50 µg/ml). Os resultados coincidem com trabalhos anteriores que indicam que em bactérias patógenas a resistência a antibióticos está associada à resistência a metais pesados. [Int Microbiol 2004; 7(3):213-218]

Palavras chave: galerias pluviais · contaminação fecal · metais pesados · resistência a antibióticos



Exposure to contaminated water, by ingestion as drinking water or from recreational activities, is a significant pathway for the transmission of gastrointestinal pathogens. Swimming or bathing in contaminated waters has often been associated with a higher risk of gastrointestinal disease. The WHO estimates that 2.1 million people die annually from diarrheal diseases and that 10% of the population of the less-industrialized world suffers from parasitic worm infections related to improper waste and excreta management. In the northeastern region of Brazil alone, about 17,300 children die every year from infectious diseases related to poor water and food sanitation []. Currently, Escherichia coli is one of the main pathogens responsible for gastroenteritis in children in Brazil [16], where several pathogenic categories of the bacterium have been recognized, including enterotoxigenic (ETEC), enteroinvasive (EIEC), enterohemorrhagic (EHEC), enteropathogenic (EPEC) enteroaggregative (EAggEC) and enteroadhesive (DAEC) [10,16,17].

Sources of contamination of surface water include urban and farm runoff, discharges from wastewater treatment facilities, wildlife, and storm sewers. Controlling the quality of water discharged from urban areas into water along the coastline is a priority. Research is essential in order to identify pollution sources and types, and to assess risk, which involves integrating scientific data regarding an environmental hazard into a framework that addresses the risk of exposure and the potential health impacts [18]. Armed with this information, advice can be transmitted to the general public and when required, prevent beach-goers and bathers from being exposed to elevated levels of enteric contaminants and other pathogens capable of causing intestinal, skin, ear and throat infections.

The objective of this work was to establish and characterize the pollution distribution patterns of pathogens reaching Natal's coastline from storm sewers in order to provide baseline data for better city sanitation. To do so, the concentrations of fecal coliform bacteria in samples drawn from storm sewers and their receiving waters on the eastern waterfront of the city of Natal were estimated and correlated with rainfall indices on the days prior to sampling. Furthermore, E. coli strains were isolated and characterized with respect to serogroup, resistance to heavy metals and resistance to antibiotics in order to assess their pathogenic diversity and dynamics.

Materials and methods

Sampling location. Three beach locations along the waterfront of Natal, Rio Grande do Norte, Brazil were selected on the basis of their popularity and intense leisure use and because they receive large amounts of runoff water from the city's storm sewers. The sites investigated were Praia do Meio (PM), Areia Preta (AP) and Ponta Negra (PN) (Fig.1).

Sampling. A total of 72 samples-12 from each of the three storm sewers and adjoining beach locations (PM, AP and PN)-were collected during the period January-June, 2002. Sampling was carried out weekly, and randomly with respect to tides, which were registered only as flooding or ebbing. The water samples were placed in sterile 1000-ml amber-colored bottles and transported in iceboxes to the laboratory for immediate processing.

Isolation of fecal coliforms. Fecal coliforms from the samples were determined by standard multiple-tube fermentation methods [1]. The strains were identified biochemically according to the method of Hitchins et al. [12]. Strains classified as E. coli were maintained on trypticase soy agar (TSA) (Difco, Detroit, MI).

Antigen analysis. The antigenic characteristics of purified isolates were evaluated using polyvalent and monovalent somatic antisera for the enteropathogenic group (O18, O25, O26, O44, O55, O86, O91, O111, O112ab, O119, O124, O125, O126, O127, O128, and O158) and the enteroinvasive group (O28, O29, O112ac, O124, O143, O144, O152 and O164). The antisera were prepared by the Oswaldo Cruz Foundation using the rapid slide seroagglutination technique [8].

Resistance to antibiotics. Serogroup strains were tested for resistance to nalidixic acid (30 µg), ampicillin (10 µg), cephalothin (30 µg), cefoxitin (30 µg), ceftriaxone (30 µg), ciprofloxacin (5 µg), chloramphenicol (30 µg), gentamicin (10 µg), imipenem (10 µg), nitrofurantoin (300 µg), sulfametoxazol-trimethoprim (23.75/1.25 µg) and tetracycline (30 µg) by using the disk diffusion method of Bauer et al. [3] and following the recommendations outlined in NCCLS [13]. The standard control strains were Escherichia coli ATCC 25922 and Staphylococcus aureus ATCC 25923, the acceptable inhibition zone variations for which may be found in NCCLS [13].

Resistance to metals. Using the plate dilution technique described by Elek and Higney [7] and Dias et al. [6], aqueous solutions of CuSO4 and ZnSO4 were incorporated in Mueller Hinton agar at concentrations 100, 150, 200 and 250 µg/ml. HgCl2 was incorporated at concentrations 5, 10, 20, 30, 40, and 50 µg/ml. Metal-free control plates and the control strain Escherichia coli ATCC 25922, which is susceptible to Cu, Zn and Hg, were used to evaluate the viability of the strains and culture media.

Rainfall indices. Data on rainfall indices from the day preceding each sampling were retrieved from the Meteorological Service of the Federal University of Rio Grande do Norte.

Statistical analysis. The levels of contamination in the water samples collected from storm sewers and adjacent seashores were compared by analysis of variance (ANOVA). Average values obtained were compared by the Tukey test at p < 0.05. The correlation between rainfall and fecal coliform counts in the samples was measured by the Pearson correlation test (p < 0.05). Statistical analyses were done using the software Statistics for Windows [Statsoft Inc., Tulsa, OK, USA, 1996].

Results and Discussion

The water samples from the storm sewer and adjacent seashore of the sampling location at AP were the most polluted. Levels of fecal coliform contamination remained high throughout the study period and differed significantly (p < 0.05) from those of the other two locations (Table 1 and Fig. 2). Of the 12 samples collected from the storm sewer at AP, five (41.7%) yielded values higher than 1.1 × 107 FC/100 ml, whereas the values obtained for the remaining samples ranged from 4.3 × 105 to 1.1 × 107 FC/100 ml. The discharge pipe of the storm sewer at AP is fitted into a 3-m high cement wall on the beach and produces a continuous flow of wastewater in both dry and wet seasons, with clear visual and olfactory signs of pollution. Of the 12 seawater samples collected in front of the discharge point at AP, two (16.6%) also yielded coliform numbers higher than 1.1 × 107 FC/100 ml. Children often play and bathe in a depression at this location, where seawater is trapped during low tide and mixes with highly contaminated wastewater. Only one (8.3%) of the 12 samples from the storm sewer discharging at PM yielded values of the most probable number (MPN) above 1.1 × 107 FC/100 ml. At this sampling site, in the sand, there was a large puddle of dark, stinking contaminated water. Seawater samples collected in front of this discharge point yielded coliform counts that ranged from 9.3 × 10 to 4.3 × 105 FC/100 ml (Table 1). At PN, a clandestine 20-cm-wide polyvinylchloride (PVC) wastewater pipe had been connected to the outlet of the storm sewer. The alignment of this structure suggested that it came from a nearby hotel. The flow from that pipe was continuous and formed a rivulet running towards the sea (see Fig. 1). Of the 36 seawater samples tested from the three locations (PM, AP and PN), 25 (69.4%) had fecal coliform counts above the legally permitted amount, which implied that those beaches were unsuitable for bathing.

Storm water runoff from urban areas is a major source of microbial contamination of surface waters and accounts for a significant share of the pollution occurring in coastal waters. Fecal material and other residues present on impervious surfaces, including tarmac, roofs, sidewalks, patios, bedrock outcrops and compact soil, are washed off and carried along with rainwater to the nearest body of water [2,15]. For example, more than half of the beach-water quality failures in Santa Monica Bay, California, USA, are associated with rainfall events, even though it usually rains less than 15 days per year [20]. A study of the Atlantic shoreline of Concord, New Hampshire, USA, showed that concentrations of E. coli in standing waters increased after rainfall and the arrival of storm water, and returned to baseline levels soon after the storm flow had ceased [5]. In Natal, however, there was no correlation (p > 0.05) between rainfall indices and FC counts at the three beach locations investigated. In fact, there were high levels of contamination on both rainy and dry days (see Table 1). Thus, our results suggest an irregular use of the storm sewers.

A total of 64 isolates were identified as E. coli; 37 from storm sewer samples and 27 from seawater samples. Of these, four were characterized as EIEC and two as EPEC. Of the four EIEC samples, two came from storm sewer samples and belonged to serogroup O112ac, one came from the shore of PM and was identified as serogroup O124, and one, which we labeled serogroup O143, came from seawater collected at AP. The two EPEC isolates belonged to serogroups O111 and O125 and were detected in storm sewer water samples collected at PN. Similar serogroups had been previously isolated from water samples collected at several seaside resorts in Brazil [11,17,24]. Only a few strains were identified as EPEC and EIEC, and the identification process was restricted to serogroups. However, the relevance of this finding should not be underestimated. Trabulsi et al. [22] described the division of EPEC strains into typical and atypical. The two groups differed from each other with respect to several characteristics. Typical EPEC strains are a leading cause of infantile diarrhea in developing countries, whereas atypical EPEC strains are becoming an increasingly frequent cause of diarrhea in industrialized countries. The same shift might be occurring in Brazil. Humans are the only reservoir for typical EPEC, whereas both humans and other animals can serve as reservoirs of atypical EPEC. In addition to the geographical differences in their occurrence, typical and atypical EPEC also differ in their genetic characteristics, serotypes, and virulence. Atypical EPEC are more closely related to Shiga-toxin-producing E. coli.

Table 2 summarizes the response of the 64 isolates when challenged with drugs of common therapeutic use. As many as 35.9% of the strains were resistant to one or more of the antibiotics tested. The highest rates of resistance were towards ampicillin (21.8%), followed by cephalothin and sulfametoxazol-trimethoprim (18.7%) and tetracycline (14.1%). By contrast, resistance rates were low towards nitrofurantoin (3.1%), nalidixic acid (4.7%) and chloramphenicol (1.6%). All the strains tested were found to be susceptible to cefoxitin, ceftriaxone, ciprofloxacin, gentamicin, and imipenem. E. coli strains isolated from beaches in Fortaleza in 1996 and identified as serogroups O55 and O125 were also shown to be resistant to cephalothin and ampicillin [23]. Antibiotic-resistance analysis of fecal coliforms may be used to determine sources of fecal contamination, and aid in water-quality improvement [4]. The increase in microbial resistance to antibiotics has made the management of infections more difficult and has contributed to the growing cost of public health care.

Table 3 shows that all strains were resistant to Cu and Zn at concentrations of 250 µg/ml, whereas 23.4% of the isolates were resistant to 50 µg Hg/ml. According to Nies [14], mercury is much more toxic to E. coli than zinc, whose action resembles that of other elements of lower toxicity, such as copper, nickel and cobalt. In general, the isolated strains were highly resistant to heavy metals at the concentrations tested. The association between heavy-metal resistance and antibiotic resistance was marked. Of the 64 E. coli strains investigated, 24 (37.5%) were resistant to at least one antibiotic in combination with two or three metals. Our results therefore agree with the findings of Filali et al. [9].

Despite the extensive sanitation programs carried out by local authorities in Natal, similar to those undertaken in other geographical regions, pollution continues to be a cause of concern. Identifying the sources of fecal pollution in water is paramount in assessing the potential human health risk involved as well as in prescribing necessary remedial action. New methodologies are now being employed to identify the pathogens and their sources [19,21]. The application of molecular biology techniques to address questions concerning water quality is very promising and may offer the next generation of tools for researchers and regulators to continue their fight for better sanitation.


1. American Public Health Association (APHA) (1995) Standard methods for the examination of water and wastewater. 19th ed. Washington, DC        [ Links ]

2. Arnold CL, Gibbons CJ (1996) Impervious surface coverage: the emergence of a key environmental indicator. Amer Planning Assn J 62:243-258        [ Links ]

3. Bauer AW, Kirby WMM, Sherris JC, Turck M (1996) Antibiotic susceptibility testing by a standardized single disc method. Amer J Clin Pathol 45:493-496        [ Links ]

4. Burnes BS (2003) Antibiotic resistance analysis of fecal coliforms to determine fecal pollution sources in a mixed-use watershed. Environ Monit Assess 85:87-98        [ Links ]

5. Comstock G (1997) Stormwater characterization study. NHDES-WD-91-12.NH Department of Environmental Services, Concord, NH        [ Links ]

6. Dias JCAR, Vicente ACP, Hofer E (1987) Coliformes fecais em águas de esgotos: I - Resistência a antibióticos, metais pesados e colicinogenia. Mem Inst Oswaldo Cruz 82:335-343        [ Links ]

7. Elek SD, Higney L (1970) Resistogram typing-A new epidemiological tool: Application to Escherichia coli. J Med Microbiol 3:103-110        [ Links ]

8. Ewing WH, Edwards PR (1986) Edward and Ewing's identification of Enterobacteriaceae, 4th ed, Elsevier, New York        [ Links ]

9. Filali BK, Taoufik J, Zeroual Y, Dzairi FZ, Talbi M, Blaghen M (2000). Wastewater bacterial isolates resistant to heavy metals and antibiotics. Curr Microbiol 41:151-156        [ Links ]

10. Gomes TAT, Rassi V, MacDonald KL, et al. (1991) Enteropathogens associated with acute diarrheal disease in urban infants in São Paulo, Brazil. J Infect Dis 164:331-337        [ Links ]

11. Gonçalves AG, Campos LC, Gomes TAT, Rodrigues J, Sperandio V, Whittam TS, Trabulsi LR (1997) Virulence properties and clonal structures of strains of Escherichia coli O119 serotypes. Infect Immun 65:2034-2040        [ Links ]

12. Hitchins AD, Feng P, Watkins WD, Ripley SR, Chandler LA (1992) Escherichia coli and the coliforms. Bacteriological Analytical Manual. 7th ed. American Public Health Association (APHA), Washington, DC, pp. 27-29        [ Links ]

13. National Committee for Clinical Laboratory Standards (NCCLS) (2002) Performance Standard for antimicrobial susceptibility testing. 12th Informational Supplement. NCCLS document M100. NCCLS, Wayne, PA, vol. 22, 123 pp.         [ Links ]

14. Nies DH (1999) Microbial heavy-metal resistance. Appl Microbiol Biotechnol 51:730-750        [ Links ]

15. Reeves RL, Grant SB, Mrse RD, Copil Oancea CM, Sanders BF, Boehm AB (2004) Scaling and management of fecal indicator bacteria in runoff from a coastal urban watershed in southern California. Environ Sci Technol 38:2637-2648        [ Links ]

16. Rodrigues J, Acosta VC, Candeias JMG, Souza LO, Filho FJC (2002) Prevalence of diarrheogenic Escherichia coli and rotavirus among children from Botucatu, São Paulo State, Brazil. Brazilian J Med Biol Res 35:1311-1318         [ Links ]

17. Rosa AC, Mariano AT, Pereira AM, Tibana A, Gomes TAT, Andrade JR (1998) Enteropathogenicity markers in Escherichia coli isolated from infants with acute diarrhoea and healthy controls in Rio de Janeiro, Brazil. J Med Microbiol 47:781-790        [ Links ]

18. Rose JA, Grimes DJ (2001) Reevaluation of microbial water quality: Powerful new tools for detection and risk assessment. American Academy of Microbiology. Available at: bid=2156 (checked on July 8, 2004)        [ Links ]

19. Seurinck S, Verstraete W, Siciliano SD (2003) Use of 16S-23S rRNA intergenic spacer region PCR and repetitive extragenic palindromic PCR analyses of Escherichia coli isolates to identify nonpoint fecal sources. Appl Environ Microbiol 69:4942-4950        [ Links ]

20. Schiff KC, Morton J, Weisberg SB (2003) Retrospective evaluation of shoreline water quality along Santa Monica Bay beaches. Mar Environ Res 56:245-253        [ Links ]

21. Scott TM, Parveen S, Portier KM, Rose JB, Tamplin ML, Farrah SR, Koo A, Lukasik J (2003) Geographical variation in ribotype profiles of Escherichia coli isolates from humans, swine, poultry, beef, and dairy cattle in Florida. Appl Environ Microbiol 69:1089-1092        [ Links ]

22. Trabulsi LR, Keller R, Gomes TAT (2002) Typical and atypical enteropathogenic Escherichia coli. Emerg Infect Dis 8:508-513        [ Links ]

23. Vieira RHSF, Evangelista NSS, Rodrigues DP (1996) Colimetria das águas marinhas de Fortaleza, Brazil e detecção de cepas de Escherichia coli enteroinvasora (EIEC) e enteropatogênica clássica (EPEC). Arq Cien Mar 30:27-31        [ Links ]

24. Vieira RHSF, Rodrigues DP, Evangelista NSS, Teophilo GND, Reis EMF (1998) Colimetry of marine waters off Fortaleza, Brazil and detection of enteropathogenic Escherichia coli strains. Int Microbiol 1:221-224        [ Links ]

Creative Commons License Todo el contenido de esta revista, excepto dónde está identificado, está bajo una Licencia Creative Commons