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Brazilian Journal of Biology

Print version ISSN 1519-6984

Braz. J. Biol. vol.72 no.3 São Carlos Aug. 2012

https://doi.org/10.1590/S1519-69842012000300009 

ECOLOGY

 

Genotoxicity and toxicity evaluations of ECF cellulose bleaching effluents using the Allium cepa L. Test

 

Genotoxicidade e toxicidade em Allium cepa L.: avaliação da qualidade do efluente no processo de branqueamento da celulose

 

 

Roa, O.I; Yeber, MC.I,*; Venegas W.II

IFaculty of Science, Universidad Católica de la Santísima Concepción, P.O. Box 297, Concepción, Chile
IIDepartment of Cellular Biology, Universidad de Concepción, P.O. Box 160-C, Concepción, Chile

 

 


ABSTRACT

Toxicity and genotoxicity tests were performed on root cells of Allium cepa in order to evaluate wastewater quality following an ECF cellulose bleaching process. The results revealed a toxic effect of the effluent, with inhibition of meristem growth and generally lower values of metaphase, anaphase and telophase indices at pH 10.5 than pH 7 for all effluent concentrations. The genotoxicity effect was different from the toxic effect given that the micronucleus and the chromosomal aberration tests in anaphase-telophase cells were low over all ranges of the studied effluent concentrations.

Keywords: Allium cepa, toxicity, genotoxicity, ECF bleaching effluent, Kraft cellulose.


RESUMO

Os testes de toxicidade e genotoxicidade foram realizados em células da raiz de Allium cepa, a fim de avaliar a qualidade do efluente na sequência de um processo de branqueamento de celulose ECF. Os resultados revelaram um efeito tóxico do efluente, com inibição de crescimento do meristema e valores geralmente baixos de metáfase, anáfase e índices de telófase, a pH 10,5 e pH 7, para todas as concentrações do efluente. O efeito de genotoxicidade foi diferente do efeito tóxico, uma vez que o micronúcleo e os testes de aberrações cromossômicas em anáfase-telófase das células foram baixos em todas as gamas de concentrações do efluente estudado.

Palavras-chave: Allium cepa, toxicidade, genotoxicidade, branqueamento por sequências ECF, Kraft celulose.


 

 

1. Introduction

Pulp and paper mill effluents are constant sources of discharge of a complex mixture of organic pollutants, which produce aquatic contamination and impact human health. Examples of this type of contamination are given by various authors (Grant, 1982; Blavk and Bauman, 1991; Garcia et al. 1995; Bowron et al., 2009; Diniz et al., 2010; MacLatchy et al., 2010; Kulshreshtha et al., 2011), who report that the cellulose and paper industry release a large quantity (i.e. metric tons) of chemical agents into aquatic areas. Many of these agents are mutagens, and some are carcinogenic for humans. Thus, scientific studies have detected both toxic and genotoxic effects caused by the liquid effluents dumped into the aquatic environment. The common onion, Allium cepa L. (2n = 16), constitutes a very convenient test system for estimating the harmful effects of chemicals on biological materials. The A. cepa assay is an efficient test for chemical screening and in situ monitoring of the genotoxicity effect of environmental contaminants (Fiskesjö, 1985, 1993; Barbérico et al., 2009; Siddiqui et al., 2011; Nunes et al., 2011). This test has been widely used to study the toxicity and genotoxicity of many dangerous contaminants, such as pesticides, azo dyes, food preservatives and hydrocarbons (Riffat and Ahmad, 2006; Mittergger et al., 2007; Feretti et al., 2007; Türkoğlu, 2007; Leme and Marin-Morales, 2008; Mustafa and Arikan, 2008; Ashraf and Husain, 2010), where all tests have shown that A. cepa is more sensitive for detecting toxicity and genotoxicity than other tests. Studies conducted with real effluents obtained from a textile mill revealed that water contaminated with azo dyes induces chromosomal and nuclear aberrations in A. cepa (Caritá and Marin, 2008; Leme and Marin-Morales, 2009). Pulp and paper mill effluents are a complex mixture of organic compounds derived from lignin (Quevedo et al., 1994; Strömberg et al., 1996; Xavier et al., 2011) However, today mills have made significant changes in their processes, partially or totally eliminating elemental chlorine as a bleaching agent. This bleaching sequence, known as Elemental Chlorine Free (ECF) or Totally Chlorine Free (TCF), achieves the reduction of organochloride compounds, such as Absorbable Organic Compounds (AOX), however, toxic and inhibitory organic compounds continue to be present in the effluents. Therefore, in this study, we use the Allium cepa test to evaluate the toxicity and genotoxicity of a Kraft ECF bleaching effluent.

 

2. Material and Methods

2.1. Effluent collecting

The effluent was obtained from the bleaching sequence of Kraft cellulose from radiata pine (Pinus radiata) Kraft cellulose from an industry, specifically obtained from the first extraction stage of the ECF bleaching sequence (E1). Prior to its use, the effluent was left at room temperature (18‑20 ºC). The first stage of this study consisted of evaluating the effluent concentrations: the preliminary study began with toxicity assays, evaluating three concentrations (100%, 50%, and 25%), but due to high toxicity we added a fourth concentration of 6.25%. Spring water was used for the dilutions and, prior to each treatment, the pH, temperature, and conductivity were measured with VARIO CAND SET WTW 2X00-001A equipment. The compounds present in the effluent were analyzed on a Shimadzu AOC-5000 gas chromatography-mass spectrometer (GC/MS).

2.2. Toxicity assay

For the acute toxicity assay, 42 dry Allium cepa bulbs (5-6 cm diameter) with no leaf or root formation were selected. Prior to the experimental set up (Figure 1), the bulbs were cleaned, to eliminate the dried epidermis, using a scalpel to remove the tissue remains and dry roots from around the root area, avoiding damage to the primary roots. For the experiment, 42 flasks, each with an 80 mL capacity, were divided into six groups of seven flasks. Each group was labelled according to the concentration of the experimental dilutions: 100%, 75%, 50%, 25%, 6.25%, and the corresponding negative control (spring water). Simultaneously, a positive control was set apart to detect whether this protocol provides a feasible way to evaluate the toxicity of effluents. The positive control required the use of 42 bulbs (prepared as above) with different CuSO4 solutions (10, 20, 40, 80, and 100 mg/L) (Rank et al., 2002). In the initial stage of assembly of the test, we selected a copper sulfate soluble compound, purity ≥99%, which was subjected to toxicity tests to establish the concentration range that produces the desired effect. The dose-response curve was used as a toxicant reference. Given that this is a semi-static assay, it was left at room temperature (18‑20 ºC), with indirect light, for 72 hours. Observations were made once a day in order to detect possible volume loss due to evaporation or absorption during the treatment.

 

 

At the end of the exposure period, we recorded a root length using a calliper. With this technique, we made an estimate of the minimum and maximum length of the roots in each graduated flask, and used the mid-point. The data were entered into the TOXSTAT program version 3.4 in order to evaluate test assumptions and to determine the concentration for which there were significant differences in order to infer that the effluent significantly inhibited the growth of the bulb roots.

2.3. Mitotic index determination

The mitotic index was calculated by quantifying 2,000 cells in a cellular preparation (three slides = 6,000 total cells) observed under a Zeiss binocular microscope Standard R.A. The cells were classified according to their stage in the cellular cycle (i.e. interphase, prophase, metaphase, anaphase or telophase). These data were used to calculate the indices for evaluating toxicity at the cellular level, using the following formulae:

Mitotic index (%) = Number of cells in mitosis × 100/total number of cells

Calculation of the Phase Index:

Index in each phase (%) = Number of cells in each phase × 100/total number of cells in mitosis

2.4. Genotoxicity assays

In this experiment, we used A. cepa bulbs exposed to the same effluent concentrations as above (100%, 75%, 50%, 25%, and 6.25%), as well as a negative control using spring water and a positive control using 10 mg.L–1 of methyl methanesulfonate (MMS) (Rank et al., 2002).

Each experimental concentration was replicated in triplicate. During the first part of the experiment, the meristems were left for 46 hours to allow for germination in 100 mL graduated flasks, placed in a dark chamber, at room temperature, under continuous aeration. For each treatment, we quantified the presence of micronuclei (MN) during interphase and chromosomal aberrations (CA) during anaphase-telophase (A-T). The experiment was conducted in a dark chamber with a continuous aeration system.

After the germination period, the best apical meristems were selected from each concentration and replicate. The selected meristems were cut and placed in small flasks with Carnoy's fixative (3:1, absolute alcohol:acetic acid) for 24 hours. The meristems were then washed in distilled water and subjected to acid hydrolysis in a test tube for 10 minutes at 60 ºC in a double boiler. Following this period, the test tube was quickly cooled using tap water in order to stop the hydrolysis and the meristems were then washed with distilled water.

The cell nuclei were stained with Schiff's reagent for 20 to 30 minutes. Each apical meristem was then macerated in 30% acetic acid and deposited on a slide. In order to separate the cover from the slide without harming the sample, it was frozen on dry ice. The cytological preparations were then examined under a photomicroscope to determine the MN frequency by quantifying the percentage of chromosome aberrations in A-T in 1000.

 

3. Results and Discussion

The initial conditions of the effluent were as follows: temperature of 18 ºC, conductivity 0.56 KΩ/cm, and pH 10.5. Since the initial pH of the effluent was alkaline, for adequate performance of the toxicity test it was necessary to add a test at pH 7.0 in order to normalize the experiment.

The analysis of the results showed a clear toxic effect of the studied effluents, as reflected in the inhibition of meristem growth, when the bulbs were stimulated to grow under higher concentrations of the effluent. This finding was corroborated with the results of finer cellular toxicity studies, which showed a decrease in the mitotic index when the A. cepa apical meristems were divided and exposed to a high concentration environment, as was the case of the initial effluent concentration (100%) (Figure 2). On the other hand, the metaphase, anaphase, and telophase indices presented results in accordance with those indicated earlier; that is, a noteworthy decrease of the phase indices as the effluent concentrations increased (Figure 3). The opposite pattern was observed in the results obtained from the genotoxicity studies. In fact, the MN frequency and percentage of chromosomal aberrations in A-T were unexpectedly low (Table 1), indicating that the industrial analyzed effluent is toxic but does not have genotoxic properties.

 

 

In order to evaluate the possible effect of the pH, toxicity and genotoxicity studies were performed at pH 10.5 and pH 7 in order to establish differences in the results of toxicity and genotoxicity under both conditions. The results obtained in this experimental design indicated that the effluent was clearly more toxic at pH 10.5 than at pH 7, with significant differences in the acute toxicity assay. The same tendency was observed in the cellular toxicity test; however in this case, the results were more related to the pH of the original effluent than to the presence of genotoxic components in the complex mixture of chemical substances present in the effluent. With respect to the genotoxicity assay, it is interesting to note that MN frequencies and chromosome aberrations were found in anaphase-telophase were greater at pH 7 than at pH 10.5 (Table 1). This indicates that at pH 10.5, the effluent produces a toxic effect in relation to the cell division, either inhibiting it or promoting a lengthening of the cellular cycle, but does not have a genotoxic effect. The photomicrographs show the presence of MN found in Allium cepa cells during interphase (Figure 4a), and chromosomal aberrations consisting of acentric fragments, rings and acentric chromosomes (Figures 4b, c, and d). Micronuclei (MN) were present in more than 50% of cells at high effluent concentrations (i.e. 100%, 75%) at pH 7, while at pH 10.5, percentages fell to below 25% but were also present at low effluent concentrations (25%) (Table 1). Chromosomal aberrations (CA) in A-T were present at all concentrations except the control (0 effluent), and were higher at pH 7 than pH 10.5 (Table 1). We observed significant differences in prophase, metaphase, anaphase and telephase indices, however the mitotic index was highly variable for both factors and no significant differences were observed for this index (Figure 2). For the majority of these indices, we observed a significant interaction between concentration and pH, which were generally higher at pH 10.5 than at pH 7 for different concentrations of effluent (Figure 3). It should be considered that decreasing the pH from 10.5 to pH 7 might allow potential clastogenic agents present in the complex mixture to be masked by the pH and to act on the hereditary material, damaging it through complex molecular mechanisms related to changes in pH.

By chromatographic analysis (Figure 5), it was possible to identify two chlorinated compounds (biphenyl-2, 7-dichloride methylene-4, 5-dicarboxylic and anhydride biphenyl-2-chlorophenyl-4, 5-phthalic). The environmental consequences of these emissions could be serious. Much research conducted near industries with these chlorinated compounds in their effluents has detected a high frequency of anomalous fish with neoplasia (Vogelbein et al., 1990; Ohe et al., 2004; Misik et al., 2011).

Given that government agencies worldwide have adopted legislation to reduce the emissions of toxic waste from industries, many researchers have made efforts using modern technology to protect the aquatic environment. This provides some degree of optimism with respect to improvements in the interface between industry and the environment and potential solutions for cleaning-up the aquatic environment. Nevertheless, scientists and researchers should always be alert since molecules that have not been eliminated by the different treatments applied to effluents from the cellulose industry, and which are considered to be harmless to the aquatic biota, could produce various changes and/or modifications at the molecular and cellular levels in organisms that inhabit these environments. These changes can range from alterations in metabolic functions, such as enzymatic detoxification activity, to alterations in the reproductive system. These molecules, called endocrine disruptors, have been detected in effluents from the cellulose industry (Venegas et al., 1994, 1995; Wang et al., 2008; Kovacs et al., 2011). Since these molecules have a chemical structure similar to steroid molecules, they can cause exaggerated growth of immature oocytes of native fish and other aquatic organisms, and alter their reproductive performance. The specific effects of these molecules on organisms are variable since these biological effects are exerted in the context of a genotype-environment interaction.

It is essential to make clear that both in toxicology and in vivo studies of genotoxicity of samples from continental aquatic environments, the use of the plant model, Allium cepa has several advantages given that it is easy to manipulate, it is sensitive to rapid response bioassays, it is cheap, and, most importantly, it has a good correlation with models that use mammalian cells for this type of study (Fiskesjö, 1997; Venegas et al., 1990; Oberholster et al., 2008; Chaparro et al., 2010). Finally, the Allium cepa L. test proved to be a sensitive method, representing an efficient model for detecting the effects of different contaminants on the environment, such as those associated with cellulose effluents. It is important to note that it may be possible to perform continuous monitoring using the Allium cepa L. test, thus obtaining a rapid response of the effects of contaminants in the environment. These effluents can change their toxicity due to changes in pollutant concentrations, by dilution or changes in the pH, or due to the type of raw material used for the production of cellulose. As was observed in this study, the toxicity response was most affected by changes in the pH, due to the high pH of this type of effluent.

Acknowledgements – The authors would like to thank the Faculty of Science, Universidad Católica de la Santísima Concepción and the Department of Cellular Biology, Universidad de Concepción.

 

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Received July 5, 2011
Accepted August 22, 2011
Distributed August 31, 2012

 

 

*e-mail: mcyeber@ucsc.cl

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