Applied and Environmental Soil Science

Applied and Environmental Soil Science / 2012 / Article
Special Issue

Biosolids Soil Application: Agronomic and Environmental Implications 2012

View this Special Issue

Research Article | Open Access

Volume 2012 |Article ID 518206 |

Cintya Ap. Christofoletti, Annelise Francisco, Carmem S. Fontanetti, "Biosolid Soil Application: Toxicity Tests under Laboratory Conditions", Applied and Environmental Soil Science, vol. 2012, Article ID 518206, 9 pages, 2012.

Biosolid Soil Application: Toxicity Tests under Laboratory Conditions

Academic Editor: Leonid Perelomov
Received05 Jan 2012
Revised05 Apr 2012
Accepted26 Apr 2012
Published30 Jul 2012


A large volume of generated sewage sludge makes its disposal a problem. The usage of sludge in agriculture is highlighted by a number of advantages. However, heavy metals and other toxic compounds may exercise harmful effects to soil organisms. This study evaluated the possible toxic effects of a biosolid sample, under laboratory conditions, for 30 days, using diplopods Rhinocricus padbergi and plants Allium cepa (onion) as test organisms. The data obtained demonstrated that the biosolid raw sample had genotoxic potential for Allium cepa root tip cells. In the diplopods exposed to biosolid sample, epithelium disorganization in the midgut and a reduction of the volume of the hepatic cells were observed after 7 days of exposure. After 30 days, the animals still showed a reduction of the volume of the hepatic cells, but in minor intensity. Allium cepa analysis showed genotoxicity, but this effect was reduced after 30 days of bioprocessing by diplopods. This study was important to know the effects as well as to determine how this waste could be applied concerning the soil living organisms and plants.

1. Introduction

In sewage treatment plants (STP), after the sewage had been treated, a sludge rich in organic matter and nutrients is generated as a waste, known as sewage sludge. The composition of this sludge is very variable since it depends on the source of the sewage treatment process and the seasonality [1]. Generally, the sewage sludge presents around 40% to 60% of organic matter, 4% nitrogen, 2% phosphorus, and other macro- and micronutrients, besides potentially toxic elements [2].

The generated sewage sludge still can go through processes in order to increase the solids and reduce the number of pathogenic organisms, generating a residue called biosolid, which is considered most innocuous than the sewage sludge itself [3]. Good quality fertilizers can be generated with the sludge stabilization, reducing its volume through the use of “sludge thickeners drying beds,” filter presses, band presser, vacuum filters, and centrifugation [4]. According to Lambais and Do Carmo [5], chemical composition of the sludge depends on the origin of the wastewater. This way, the material is variable, but generally it is a compound rich in organic matter and essential nutrients for plants and microorganisms.

Currently, sewage treatment plants in different Brazilian cities are facing the problem of sludge disposal. The alternatives to the sewage sludge usual fate are landfill disposal, reuse in industry (light-weight aggregate production, bricks and ceramics manufacturing, and cement production), incineration, conversion into fuel oil, ocean disposal, recovery degraded soils, and agricultural use [2, 6].

In Brazil, there is a preference for the use of sludge in agriculture, since there is a considerable land availability and the costs would be relatively low. However, this practice is still incipient, so that the application is made without an adequate management [4]. According to Melo et al. [7], when incorporated into the soil, sewage sludge provides changes in physical properties such as density, aggregates size, and water retention capacity; on chemical properties such as pH, electrical conductivity, CEC, and increased levels of P and N and biological properties, usually by increasing soil microbial activity.

However, the main limitation observed during the evaluation of possible utilization of sewage sludge in agriculture refers to the presence of metals and other persistent pollutants [8], which may be toxic to plants [9], microorganisms [10], and soil invertebrates [11]. Although other work related the phytoavailability of these metals to a variety of cultures, few studies relate the sewage sludge to genotoxic and mutagenic potential. The application of metal-rich biosolids in clay and sandy soils, compared with biosolids with low-metal concentration, causes a transient soil microbial community increase in mass and activity, with reduced carbon immobilization [5]. Many field studies, based on biosolids agronomic doses, reported soil biota stimulation, probably due to the addition of organic matter, which causes an increase in fertility. The application of this kind of compound, however, has shown inhibitory effect on soil invertebrates [12].

Thus, the aim of this study was to investigate the effects of a biosolid sample according to Brazilian standards for its application on soils, under laboratory conditions, using Allium cepa (plant) and Rhinocricus padbergi (terrestrial invertebrate) as test organisms.

2. Materials and Methods

2.1. Rhinocricus padbergi

Adult specimens of R. padbergi with a mean size of 5.0 cm were collected at the campus of the São Paulo State University (UNESP), Rio Claro, in order to avoid intraspecific differences related to either diplopod size or age. After collection, the specimens were maintained in the laboratory for 3 weeks for acclimation, in a terrarium containing soil, tubercles, and decomposing pieces of tree trunks from the capture area. The experimental temperature was 21 ± 2°C and the photoperiod was a 12 : 12-h light/dark cycle.

2.2. Allium cepa

All assays were carried out with only one kind of seeds of A. cepa (variety Baia Piriforme) to avoid different responses in the several stages of the process.

2.3. Control Soil

The control soil was obtained from the site where diplopods were collected at a depth of 0–20 cm, in the UNESP Campus of Rio Claro, SP. Soil samples were homogenized, dried at room temperature, and sieved with 4 mm mesh.

2.4. Biosolid Sample

The wastewater treatment plant where the biosolid was collected occupies an area of 20 hectares. The facility serves approximately 80% of the 318.785 inhabitants [13] of a city in São Paulo state where sewage is treated by conventional activated sludge process. In October 1999, the plant received the license of Producer of Agricultural Amendments, by the Ministry of Agriculture. The product produced in the facility is a biosolid classified as soil conditioner. The brand name is Sabesfértil (SP-09599 00001-0). Biosolid samples were collected and stored in plastic boxes wrapped with dark plastic bags and maintained in a cold room (4°C), until use.

2.5. Chemical Analysis of Samples

The concentration of trace elements (As, Ba, Cd, Cu, Cr, Hg, Mo, Ni, Pb, Se, and Zn) and the 16 priority organic compounds (PAHs) in the biosolid and control soil was determined followed the Standard Methods for the Examination of Water and Wastewater 21th Edition 2005 (SM21) and USEPA. The characterization of samples was measured by TASQA Laboratory (Paulínia, São Paulo, Brazil). Analyses of trace elements were performed by inductively coupled plasma emission spectrometry (ICP-AES). The PAHs analyses were performed by atomic absorption spectrometry. Chemical and physicochemical analyses, as well as a characterization of control soil sample based on macro- and micronutrients (N, Ca, Mg, P, K, S, Fe, Mn, Cu, and Zn), C/N ratio, organic matter, cation exchange capacity (CEC), and base-saturation percentage, were carried out by the Instituto Campineiro de Análise de Solo e Adubo (ICASA), Campinas, São Paulo, Brazil.

2.6. Calculating Biosolid Quantities for Application
2.6.1. Application of Sewage Sludge

According to the law 375/2006 of the Environmental National Council (Conselho Nacional do Meio Ambiente, CONAMA) [14], the maximum annual application of sewage sludge and derivatives in tons per hectare shall not exceed the quotient between the quantity of nitrogen recommended for the crop (in kg/ha), following the official recommendation for São Paulo State and the nitrogen content available in the sewage sludge or derivatives (in kg/t), calculated as N recommended (kg/ha)/N available (kg/t).

To determine the nitrogen available in the sewage sludge and/or biosolid, mineralization fractions were calculated. According to CONAMA [14], this fraction represents 40% of undigested and 20% of digested sewage sludge.

2.6.2. Preparation of Soil and Residue Sample for the Bioassays with R. padbergi

Two glass terraria with capacity for 22.5 L were filled with 5 Kg of control soil each. After physicochemical analysis of soil samples and biosolid, the following bioassays were set up with control soil (CS) and soil + biosolid (SB): (1)CS: 5 Kg of control soil;(2)SB: 5 Kg of control soil + 234.4 g of biosolid.

Twenty specimens of R. padbergi were then placed in each terrarium, where they remained for 30 days to assess the toxicity of contaminants present in biosolid. The animals were monitored for 90 days. Six animals per bioassay were dissected for histological analyses, three animals on the seventh day, and three diplopods in 30th day of exposure.

2.6.3. Histology of the Midgut

The diplopods were anesthetized with chloroform, placed in Petri dishes containing isotonic salt solution, and dissected under the dissecting scope. The midgut was removed and fixed in paraformaldehyde 4%. Following that, the organ was dehydrated in increasing concentrations of ethanol (70%, 80%, 90%, and 95%), embedded in resin (Leica historesin), and kept in the refrigerator for 24 h. Later, the material was transferred to plastic moulds containing inclusion resin. After polymerization, 6  m slices were obtained with the help of a Leica RM2245 microtome. For histological analyses, sections were stained with hematoxylin and eosin.

2.7. Germination of A. cepa Seeds in Residue Samples at Time 0 ( ) and after Exposure to Diplopods after 30 Days ( )

Approximately 100 seeds of A. cepa were allowed to germinate at 22°C in Petri dishes containing raw biosolid sample (B) and soil from each terrarium: CS and SB samples were collected and placed in Petri dishes for the germination of A. cepa seeds, at time 0 ( ). Positive controls were made with the aneugenic herbicide trifluralin (TRIF) at the concentration of 0.019 ppm [15] and methyl methanesulfonate (MMS), a clastogenic agent at the concentration of 10 mg/mL [16]. Negative control (NC) consisted of seeds allowed to germinate in ultrapure water and the environmental control (CS) consisted of seeds allowed to germinate in the control soil.

After 30 days of exposure by diplopods, soil samples from each terrarium were collected for the tests with onion seeds.

2.7.1. Preparation of Slides of A. cepa

After germinating and reaching 2 cm in length, root tips were collected and fixed with Carnoy (3 : 1 ethanol/acetic acid). Samples were then stained with the Feulgen reaction [17], with acid hydrolysis for 11 minutes. Root tips were sectioned to remove the meristem and region F1. To intensify the staining and spread cells, one drop of 2% acetic carmine was added. All samples were lightly pressed between slide and coverslip. Coverslips were removed with liquid nitrogen and slides were mounted with Enthelan. The material was analyzed under light microscope, at magnification of 400x.

2.7.2. Evaluation of the Cytotoxic, Genotoxic, and Mutagenic Effects on Meristematic Cells of A. cepa

A total of 5000 cells were examined for each treatment at and and for the negative and positive controls. Cytotoxicity was assessed based on morphological alterations indicating cell death, and the mitotic index (MI) calculated as MI = (number of dividing cells/total number of observed cells)   100. The cells in death process present a vacuolated cytoplasm, which is outcome of the cytoplasmatic organelles digestion by lysosomal enzymes [18]. They can still present enhanced cytoplasmatic volume, which can lead to a rupture of the plasmatic membrane exposing the cell content to the outer media [19].

Genotoxicity was evaluated based on the number of cells with chromosome aberration (CA). For the CA analyses, several aberrations within different cell divisions (metaphase, anaphase, and telophase) were considered such as C-metaphase, chromosomal adherence, multipolar anaphase and telophase, and chromosome bridge and loss [20]. The frequency of CA was calculated as CAI = (number of cells with chromosome aberrations/total number of observed cells)   100. Mutagenicity index (IMt) was determined based on the occurrence of cells with micronuclei (MN) and chromosome breaks, calculated as IMt = (total number of cells with MN and breaks/total number of observed cells)   100. The results obtained in all treatments at the different periods were compared with the negative control and soil control at their corresponding times with the Mann-Whitney test, with significance set at 0.05.

2.7.3. Evaluation of Micronuclei in Cells of the F1 Region of A. cepa

The damage to meristematic cells was assessed based on the number of micronuclei in cells of the F1 region, which is composed by differentiated cells and is located about 1 mm above the meristematic region [21]. A total of 5000 cells were examined per treatment. The results obtained for all samples were compared with the negative control and soil control at their corresponding times with the Mann-Whitney test, with significance set at 0.05.

3. Results

3.1. Chemical Characterization of Samples

To follow a Brazilian standard for application of biosolids on soil, data regarding the agronomic potential and fertility of control soil became necessary. The values obtained are presented in Table 1. The results obtained by physical-chemical and trace elements analysis of control soil and biosolid sample are presented in Table 2. The concentrations of arsenic and copper found in the control soil were above the limits determined by CETESB-195/2005-E [22], but below the limits for intervention in agricultural areas. Levels of barium, lead, copper, chromium, molybdenum, nickel, and zinc found in the biosolid were high, but below the maximum level allowed by CONAMA (Table 2). None of the 16 PAHs, priority by EPA, were detected by analyses.

SamplepHg/dm³mg/dm³mmol/dm³ TFSA%Ratio


OM: organic matter; CEC: cation-exchange capacity; V: base saturation.

ParameterSamplesMethodG (mg/kg)MCA (mg/kg)
CS (mg/kg)B (mg/kg)

Arsenic16.8<LQSM21 3120B3.541
Barium5.91158SM21 3120B751300
Cadmium<LQ<LQSM21 3120B<0.539
Total calcium25.43939SM21 3120B
Organic carbon (g/kg)12.6279SSSA Cap40
Lead49.3174SM21 3120B17300
Copper37.2276SM21 3120B351500
Electric conductivity (μs/cm)1155389SM21 3120B
Chromium31.2224SM21 3120B401000
Total sulfur15111864SM21 3120B
Total phosphorus18217027SM21 3120B
Total magnesium<LQ358SM21 3120B
Mercury<LQ1.08EPA 7470A0.0517
Molybdenum3.649.55SM21 3120B<450
Nickel13.082.3SM21 3120B13420
Nitrate (mg/Kg)4.406.79SM21 4500- E
Nitrite (mg/Kg)0.061.39SM21 4500- B
Ammoniacal nitrogen (mg/kg)31.8167SM21 4500-NH3 E
Kjeldahl nitrogen (mg/Kg)47621620SM21 4500-Norg B
pH6.208.01EPA 4095 C
Total potassium4062152SM21 3120B
Selenium<LQ<LQSM21 3120B0.25100
Total sodium<LQ<LQSM21 3120B
Solid content0.860.24SM21 2540B
Moisture (g/g)0.140.76SM21 2540B
Zinc23.2825SM21 3120B602800

CS: control soil; B: biosolid; LQ: limits of quantification; IV: inconsistent value; G: guidelines of quality for soil (mg/kg) and groundwater in São Paulo State, according to CETESB (195/2005-E); MCA: maximum concentration allowed in sewage sludge or derivative product, according to CONAMA (375/2006).
3.2. Histology of the Midgut of Diplopods

Animals from control soil presented the midgut (Figure 1(a)) as the histological pattern described for the species [23], being, therefore constituted by a pseudostratified epithelium with brush border (arrow head in Figure 1(a)). The epithelium showed principal cells with nuclei of round to oval morphology, located in middle apical region and regenerative cells in the basal portion; the epithelium is followed by a muscular layer and hepatic cells layer covered by an external membrane. The hepatic cells had an irregular morphology, spherical nucleus, and cytoplasm with cytoplasmic granules of varied content. Among the hepatic cells, some hemocytes were observed, generally isolated.

The group exposed for one week to SB showed epithelium disorganization (arrow in Figure 1(b)) with disruption in several places, indicating an epithelium renewal. The hepatic cells layer showed disorganization with volume reduction in some cells (Figure 1(c)).

After 30th day of exposure, animals from SB sample showed the minor disorganization of the hepatic cells layer when compared to the midgut of the animals exposed for 7 days (Figure 1(d)).

3.3. Cytotoxic, Genotoxic, and Mutagenic Effects on A. cepa

The mitotic index of cells examined for B, SB, TRIF, MMS, CS, and NC at 0 and after 30 days of exposure to diplopods is presented in Table 3. Seeds exposed to B and SB samples presented the highest mitotic index in both periods of exposure. However, no sample was statistically significant when compared to the negative control. In comparison to the values obtained between the CS and B samples there was a significant difference. There were no cells in the cell death process for all samples.


NC13.66 ± 1.3711.2 ± 1.781.2 ± 0.832 ± 10.2 ± 0.440.6 ± 0.54
ControlsCS14.21 ± 0.909.48 ± 1.07²2 ± 0.701.6 ± 1.140.6 ± 0.540
MMS11.53 ± 0.885.73 ± 1.158.6 ± 3.04*114.2 ± 2.94*125.6 ± 8.5*124.8 ± 7.29*1
TRIF9.47 ± 0.549.31 ± 1.3551.4 ± 8.79*123.6 ± 4.82*112.2 ± 3.42*13.6 ± 0.89*1
RawB15.36 ± 0.99NA2.15 ± 1.12NA0.16 ± 0.18NA
CombinationSB15.07 ± 0.5615.03 ± 0.7921 ± 5.83*1 *1,21.2 ± 1.30.4 ± 0.54

NC: negative control; CS: control soil; MMS: positive control; TRIF: positive control; B: raw biosolid sample; SB: soil + biosolid.
: time of mixing and : after 30 days of exposure to the diplopods.
*Statistically significant values when compared to the negative control, by Mann-Whitney test, .
1Statistically significant values when compared to the control soil, by Mann-Whitney test, .
2Statistically significant values when compared to the same treatments at 0 and 30 days.
NA: not available.

B and SB samples induced genotoxic effects (Table 3), at and ( ), characterized by chromosome aberrations, compared to the negative control and/or control soil. However, the genotoxic effect was significantly reduced after the bioprocessing by diplopods in the SB group. The most frequently observed alterations in the present study were cells in metaphase with chromosomal adherence (Figure 2(a)), polyploidy (Figure 2(b)), anaphase with chromosomal bridge (Figure 2(b)), and nuclear bud (Figure 2(c)).

Meristematic cells with micronuclei (Figure 2(d)) and chromosome breaks were examined to assess the mutagenicity. Statistical analysis revealed no mutagenic effect of the samples examined at both times of exposure compared to the negative control and/or control soil (Table 3). Although micronuclei has been observed in meristematic and F1 region (Figure 2(e)), the values were not statistically significant (Table 4) and a decrease for these values was observed after 30 days of exposure to diplopods.

F1M F1

NC0.2 ± 0.440.2 ± 0.440.6 ± 0.540.2 ± 0.44
ControlsCS0.6 ± 0.54000.2 ± 0.44
MMS21.2 ± 7.08*14.6 ± 2.07*120.6 ± 5.12*14.6 ± 0.89*1
TRIF12.2 ± 3.42*12.6 ± 1.14*3.6 ± 0.89*12.6 ± 0.89*1
RawB0.14 ± 0.140.05 ± 0.04NANA
CombinationSB1 ± 10.6 ± 0.540.4 ± 0.540

NC: negative control; CS: control soil; MMS: positive control; TRIF: positive control; B: raw biosolid sample; SB: soil + biosolid.
: time of mixing and : after 30 days of exposure to the diplopods.
*Statistically significant values when compared to the negative control, by Mann-Whitney test, .
1Statistically significant values when compared to the control soil, by Mann-Whitney test, .
2Statistically significant values when compared to the same treatments at 0 and 30 days.
NA: not available.

4. Discussion

Researches about sewage sludge disposal in soil are focused on its effects on soil fertility, plant development, and contamination by heavy metals and organic compounds [24]. However, few studies have been conducted to evaluate the toxic, genotoxic, and mutagenic potentials of the sewage sludge disposal on exposed plants and animals.

Chemical analysis of biosolid sample showed the presence of trace elements. According to the literature, these elements tend to induce genotoxic and/or mutagenic effects on plants [25, 26] and tend to concentrate in the terrestrial invertebrates tissues because their rate of absorption frequently surpasses their rate of elimination [27].

Several authors have used higher plants to diagnose and monitor the action of chemicals and environmental pollution. Among these, Allium cepa (onion) has been used in determination of cytotoxic, genotoxic, and mutagenic effects of substances [15, 28] and complex environmental samples [2936].

In this study, A. cepa assays were carried out to assess abnormalities in dividing cells and to estimate the potential of B and SB samples to induct chromosome aberrations. The mitotic index of B was statistically significant compared to control soil. In our study, the mitosis stimulation observed in B and SB treatments may be due to the phosphorus and nitrogen presence and abundant elements in domestic sewage [37, 38].

Chromosomal aberrations are recognized as important consequences of the genotoxic environmental chemicals actions [39], to which many organisms, including humans, are exposed. Epidemiological studies have linked high chromosomal aberrations frequencies at significant cancer developing risk [40]. For this reason, numerous biological tests for chromosomal aberrations evaluation have been developed, in order to ensure the environmental quality [15, 31].

The most common aberrations observed in this study were metaphase with chromosomal adherence, polyploidy anaphase, and anaphase with chromosomal bridge and nuclear bud. According to the literature, all aberrations may be caused by the action of some trace elements/metals. Some metals are potentially genotoxic/mutagenic and are strongly related to environmental pollution. Several studies with plants have shown that the genotoxic effects of metals can cause changes in chromosome structure, chromosome number, and also the disturbances in the mitotic apparatus [25, 26]; they have the ability to inhibit mitotic spindle formation, leading to an abnormal chromosomes distribution and polyploidy [25, 4143].

In this study was observed the presence of some elements such as barium, lead, copper, chromium, mercury, molybdenum, nickel, and zinc. Although their concentrations are within the standards established by CONAMA [14], according to De Godoy and Fontanetti [44], these standards do not take into account aspects such as the possible interaction of toxic metals and plants, as well as the lack of information regarding the influence of sludge on the soil fauna, including animals that promote humification, aeration, and enrichment of the same.

Like earthworms and collembola [8, 12, 45, 46], the diplopods are considered excellent test organisms for studying the organic amendment effects in the soil ecosystem due to their direct exposure and their sensibility to pollutants; therefore, the diplopods have been used as bioindicators of soil pollution and ecotoxicological assessment [27, 44, 47, 48].

The stimulation of soil biota revealed in some field studies using agronomic dosage of biosolids [49] is probably linked to the soil fertility enhancement, especially due to the contribution of the organic matter. However, in some laboratory investigations, the biosolid and sewage sludge application has caused inhibitory effects [50] and tissue damage on soil invertebrates [44, 47, 48].

Morphological changes can be employed in investigations of chemicals toxicity and in monitoring of acute and chronic effects, in impacted environments [51]. Analyses involving morphology and histology of tissues in invertebrates have been widely used to identify different damage types caused by harmful substances to animals [5255].

Preliminary histological analysis of the midgut of diplopods, exposed for 7 and 30 days to the SB sample, according to sewage sludge disposal for Brazilian law may help clarify the mechanisms used by animals in an attempt to detoxify the contaminants present in the biosolid when applied to the soil. It is inferred that the high rate of epithelium renewal of the midgut of these animals may be to maintain the integrity of the organ and an attempt by the body to compensate the damage suffered after the ingestion of contaminated soil [27]. Similar results were obtained by other authors in response to acute diplopods exposure to industrial soil contaminated with polycyclic aromatic hydrocarbons [27] and sewage sludge samples from different sewage treatment plants [47, 48].

Tissue changes related to defense and detoxification may be reversible, being present only as a result of an altered metabolic status of the organism [56]. In invertebrates, the intracellular accumulation of potentially toxic compounds in insoluble forms and in physiologically inactive ones is an efficient mechanism for detoxification of these elements [27, 57]. In diplopods, the midgut and the hepatic cells work actively in this process [47, 57].

The biotransformation of toxic compounds requires the consumption of energy reserves [27]. In the present study, after 7 days of exposure, the reduction of the volume of hepatic cells of the animals exposed to SB sample could be due to the large energy demand for detoxification of the toxic compounds found in the soil. However, after 30 days of exposure, a decrease in the aggression intensity in hepatic cells of the diplopods’ midgut was observed, probably due to SB sample stabilization.

At the same time, there was a reduction of SB genotoxicity in onion seeds exposed to this sample. It is inferred that the genotoxicity reduction was obtained again due to SB sample stabilization for bioprocessing of this by diplopods and subsequent immobilization of trace elements. However, under field conditions, the animals would be chronically exposed to this residue, given the frequent application of this. In this sense, it is indispensable to develop studies that evaluate the subchronic exposure effects in an attempt to measure whether responses are sufficient to maintain the organ integrity and/or if will elapse in more severe cellular/tissue damage.

5. Conclusion

There is evidence that biosolidsuse will lead to increased soil fertility and trace elements levels; therefore, the environmental significance of such increases needs to be examined.

The results of this study reinforce the need for more research to evaluate the biological effects of waste to be discharged into the environment in different ecosystems compartments, as well as different levels of biological organization, even when toxic agents are present at low concentrations, since the sample studied in accordance with Brazilian standards for sewage sludge disposal has shown toxic and genotoxic potential to onion seeds and terrestrial invertebrates.

In this sense, studies that evaluate the subchronic exposure effects in an attempt to measure how this provision can be harmful or not to the environment compartments and receptor organisms are necessary.


The authors would like to thank CNPq and FAPESP—Fundação de Amparo à Pesquisa do Estado de São Paulo (process number 2009/50578-3) for financial support, Américo Sampaio from SABESP—Basic Sanitation Company of the State of São Paulo, for authorizing the collection of biosolids, Dr. Paula Suares Rocha, for assistance in English language version, and Janaína Pedro-Escher, Guilherme T. Maziviero, and Juliano L. P. de Figueiredo for assistance during sampling of biosolids and experimental setup.


  1. R. P. Singh and M. Agrawal, “Potential benefits and risks of land application of sewage sludge,” Waste Management, vol. 28, no. 2, pp. 347–358, 2008. View at: Publisher Site | Google Scholar
  2. W. Bettiol and O. A. Camargo, “A disposição de lodo de esgoto em solo agrícola,” in Lodo de Esgoto: Impactos Ambientais na Agricultura, W. Bettiol and O. A. Camargo, Eds., pp. 25–36, Embrapa Meio Ambiente, Jaguariúna, Brazil, 2006. View at: Google Scholar
  3. R. J. Haynes, G. Murtaza, and R. Naidu, “Chapter 4 inorganic and organic constituents and contaminants of biosolids. Implications for land application,” Advances in Agronomy, vol. 104, pp. 165–267, 2009. View at: Publisher Site | Google Scholar
  4. C. Bertelli, Efeitos da disposição de lodos de curtume no solo e na planta [Ph.D. thesis], Universidade Estadual Paulista, São Paulo, Brazil, 2011.
  5. M. R. Lambais and J. B. Do Carmo, “Impacts ofbiosolids amendments on themicrobiota of tropical soils,” Revista Brasileira de Ciencia do Solo, vol. 32, no. 3, pp. 1129–1138, 2008. View at: Google Scholar
  6. Q. Y. Cai, C. H. Mo, Q. T. Wu, Q. Y. Zeng, A. Katsoyiannis, and J. F. Férard, “Bioremediation of polycyclic aromatic hydrocarbons (PAHs)-contaminated sewage sludge by different composting processes,” Journal of Hazardous Materials, vol. 142, no. 1-2, pp. 535–542, 2007. View at: Publisher Site | Google Scholar
  7. W. J. Melo, M. O. Marques, and V. P. Melo, “O uso agrícola do biossólido e as propriedades do solo,” in Biossólidos na agricultura, M. T. Tsutiya, J. B. Comparini, P. A. Sobrinho et al., Eds., pp. 289–363, São Paulo, Brazil, 2001. View at: Google Scholar
  8. T. Natal-Da-Luz, S. Tidona, B. Jesus, P. V. Morais, and J. P. Sousa, “The use of sewage sludge as soil amendment—the need for an ecotoxicological evaluation,” Journal of Soils and Sediments, vol. 9, no. 3, pp. 246–260, 2009. View at: Publisher Site | Google Scholar
  9. C. E. Martínez and M. B. Mcbride, “Copper phytotoxicity in a contaminated soil: remediation tests with adsorptive materials,” Environmental Science and Technology, vol. 34, no. 20, pp. 4386–4391, 2000. View at: Publisher Site | Google Scholar
  10. M. Khan and J. Scullion, “Effect of soil on microbial responses to metal contamination,” Environmental Pollution, vol. 110, no. 1, pp. 115–125, 2000. View at: Publisher Site | Google Scholar
  11. D. J. Spurgeon and S. P. Hopkin, “Comparisons of metal accumulation and excretion kinetics in earthworms (Eisenia fetida) exposed to contaminated field and laboratory soils,” Applied Soil Ecology, vol. 11, no. 2-3, pp. 227–243, 1999. View at: Publisher Site | Google Scholar
  12. N. Artuso, T. F. Kenedy, J. Connery, J. Grant, and O. Schmidt, “Effects of biosolids at varying rates on earthworms (Eisenia fetida) and springtails (Folsomia candida),” Applied and Environmental Soil Science, vol. 2011, Article ID 519485, 10 pages, 2011. View at: Publisher Site | Google Scholar
  13. Instituto Brasileiro de Geografia e Estatística,, 2010.
  14. Conselho Nacional do Meio Ambiente, “Define critérios e procedimentos para o uso de lodos de esgoto gerados em estações de tratamento de esgoto sanitário e seus produtos derivados,” Resolução number 375, Diário Oficial da União, DF, Brazil, 2006. View at: Google Scholar
  15. T. C. C. Fernandes, D. E. C. Mazzeo, and M. A. Marin-Morales, “Mechanism of micronuclei formation in polyploidizated cells of Allium cepa exposed to trifluralin herbicide,” Pesticide Biochemistry and Physiology, vol. 88, no. 3, pp. 252–259, 2007. View at: Publisher Site | Google Scholar
  16. J. Rank and M. H. Nielsen, “Allium cepa anaphase-telophase root tip chromosome aberration assay on N-methyl-N-nitrosourea, maleic hydrazide, sodium azide, and ethyl methanesulfonate,” Mutation Research, vol. 390, no. 1-2, pp. 121–127, 1997. View at: Publisher Site | Google Scholar
  17. M. L. S. Mello and B. C. Vidal, “A reação de Feulgen,” Ciência e Cultura, vol. 30, pp. 665–676, 1978. View at: Google Scholar
  18. Z. Zakeri and R. A. Lockshin, “Cell death during development,” Journal of Immunological Methods, vol. 265, no. 1-2, pp. 3–20, 2002. View at: Publisher Site | Google Scholar
  19. I. M. Cristea and M. D. Esposti, “Membrane lipids and cell death: an overview,” Chemistry and Physics of Lipids, vol. 129, no. 2, pp. 133–160, 2004. View at: Publisher Site | Google Scholar
  20. D. M. Leme and M. A. Marin-Morales, “Allium cepa test in environmental monitoring: a review on its application,” Mutation Research, vol. 682, no. 1, pp. 71–81, 2009. View at: Publisher Site | Google Scholar
  21. T. H. Ma and Z. Xu, “Validation of a new protocol of the Allium micronucleus test for clastogens,” Environmental Mutagenesis, vol. 8, no. 6, pp. 65–66, 1986. View at: Google Scholar
  22. Companhia Ambiental do Estado de São Paulo, “Valores orientadores para solos e águas subterrâneas no Estado de São Paulo,” Norma number 195/2005-E, São Paulo, Brazil, 2005. View at: Google Scholar
  23. E. R. Fantazzini, C. S. Fontanetti, and M. I. Camargo-Mathias, “Midgut of the millipede, “Rhinocricus padbergi” Verhoeff, 1938 (Diplopoda: Spirobolida): histology and histochemistry,” Arthropoda Selecta, vol. 11, pp. 135–142, 2002. View at: Google Scholar
  24. W. Bettiol and R. Ghini, “Impacts of sewage sludge in tropical soil: a case study in Brazil,” Applied and Environmental Soil Science, vol. 2011, Article ID 212807, 11 pages, 2011. View at: Publisher Site | Google Scholar
  25. G. Fisjekö, “Nucleolar dissolution induced by aluminium in root cells of Allium,” Physiologia Plantarum, vol. 59, pp. 508–511, 1983. View at: Google Scholar
  26. S. Minissi and E. Lombi, “Heavy metal content and mutagenic activity, evaluated by Vicia faba micronucleus test, of Tiber river sediments,” Mutation Research, vol. 393, no. 1-2, pp. 17–21, 1997. View at: Publisher Site | Google Scholar
  27. T. D. S. Souza and C. S. Fontanetti, “Morphological biomarkers in the Rhinocricus padbergi midgut exposed to contaminated soil,” Ecotoxicology and Environmental Safety, vol. 74, no. 1, pp. 10–18, 2011. View at: Publisher Site | Google Scholar
  28. W. F. Grant, “The present status of higher plant bioassays for the detection of environmental mutagens,” Mutation Research, vol. 310, no. 2, pp. 175–185, 1994. View at: Publisher Site | Google Scholar
  29. S. Cotelle, J. F. Masfaraud, and J. F. Férard, “Assessment of the genotoxicity of contaminated soil with the Allium/Vicia-micronucleus and the Tradescantia-micronucleus assays,” Mutation Research, vol. 426, no. 2, pp. 167–171, 1999. View at: Publisher Site | Google Scholar
  30. I. S. Grover and S. Kaur, “Genotoxicity of wastewater samples from sewage and industrial effluent detected by the Allium root anaphase aberration and micronucleus assays,” Mutation Research, vol. 426, no. 2, pp. 183–188, 1999. View at: Publisher Site | Google Scholar
  31. S. T. Matsumoto and M. A. Marin-Morales, “Mutagenic potential evaluation of the water of a river that receives tannery effluent using the Allium cepa test system,” Cytologia, vol. 69, no. 4, pp. 399–408, 2004. View at: Publisher Site | Google Scholar
  32. C. K. Grisolia, A. B. B. de Oliveira, H. Bonfim, and M. D. Klautau-Guimarães, “Genotoxicity evaluation of domestic sewage in a municipal wastewater treatment plant,” Genetics and Molecular Biology, vol. 28, no. 2, pp. 334–338, 2005. View at: Google Scholar
  33. L. C. Monte Egito, M. das Graças Medeiros, S. R. B. de Medeiros, and L. F. Agnez-Lima, “Cytotoxic and genotoxic potential of surface water from the Pitimbu river, northeastern/RN Brazil,” Genetics and Molecular Biology, vol. 30, no. 2, pp. 435–441, 2007. View at: Google Scholar
  34. R. Caritá and M. A. Marin-Morales, “Induction of chromosome aberrations in the Allium cepa test system caused by the exposure of seeds to industrial effluents contaminated with azo dyes,” Chemosphere, vol. 72, no. 5, pp. 722–725, 2008. View at: Publisher Site | Google Scholar
  35. D. M. Leme and M. A. Marin-Morales, “Chromosome aberration and micronucleus frequencies in Allium cepa cells exposed to petroleum polluted water—a case study,” Mutation Research, vol. 650, no. 1, pp. 80–86, 2008. View at: Publisher Site | Google Scholar
  36. T. S. Souza, F. A. Hencklein, D. F. Angelis, R. A. Gonçalves, and C. S. Fontanetti, “The Allium cepa bioassay to evaluate landfarming soil, before and after the addition of rice hulls to accelerate organic pollutants biodegradation,” Ecotoxicology and Environmental Safety, vol. 72, no. 5, pp. 1363–1368, 2009. View at: Publisher Site | Google Scholar
  37. B. Wang, “Cultural eutrophication in the Changjiang (Yangtze River) plume: history and perspective,” Estuarine, Coastal and Shelf Science, vol. 69, no. 3-4, pp. 471–477, 2006. View at: Publisher Site | Google Scholar
  38. C. Quiblier, C. Leboulanger, S. Sané, and P. Dufour, “Phytoplankton growth control and risk of cyanobacterial blooms in the lower Senegal River delta region,” Water Research, vol. 42, no. 4-5, pp. 1023–1034, 2008. View at: Publisher Site | Google Scholar
  39. A. T. Natarajan, “Chromosome aberrations: past, present and future,” Mutation Research, vol. 504, no. 1-2, pp. 3–16, 2002. View at: Publisher Site | Google Scholar
  40. M. G. Obe, P. Pfeiffer, J. R. K. Savage et al., “Chromosomal aberrations: formation, identification and distribution,” Mutation Research, vol. 504, no. 1-2, pp. 17–36, 2002. View at: Publisher Site | Google Scholar
  41. S. De Flora, C. Bennicelli, and M. Bagnasco, “Genotoxicity of mercury compounds. A review,” Mutation Research, vol. 317, no. 1, pp. 57–79, 1994. View at: Google Scholar
  42. G. Voutsinas, F. E. Zarani, and A. Kappas, “The effect of environmental aneuploidy-inducing agents on the microtubule architecture of mitotic meristematic root cells in Hordeum vulgare,” Cell Biology International, vol. 21, no. 7, pp. 411–418, 1997. View at: Publisher Site | Google Scholar
  43. P. C. S. Cardoso, P. L. Lima, M. O. Bahia, M. I. M. Amorim, R. R. Burbano, and R. A. F. Farias, “Efeitos biológicos do mercúrio e seus derivados em seres humanos—uma revisão bibliográfica,” Belém: Universidade Federal do Pará, View at: Google Scholar
  44. J. A. P. De Godoy and C. S. Fontanetti, “Diplopods as bioindicators of soils: analysis of midgut of individuals maintained in substract containing sewage sludge,” Water, Air, and Soil Pollution, vol. 210, no. 1–4, pp. 389–398, 2010. View at: Publisher Site | Google Scholar
  45. P. Alvarenga, P. Palma, A. P. Gonçalves et al., “Evaluation of chemical and ecotoxicological characteristics of biodegradable organic residues for application to agricultural land,” Environment International, vol. 33, no. 4, pp. 505–513, 2007. View at: Publisher Site | Google Scholar
  46. R. Moreira, J. P. Sousa, and C. Canhoto, “Biological testing of a digested sewage sludge and derived composts,” Bioresource Technology, vol. 99, no. 17, pp. 8382–8389, 2008. View at: Publisher Site | Google Scholar
  47. L. R. Nogarol and C. S. Fontanetti, “Acute and subchronic exposure of diplopods to substrate containing sewage mud: tissular responses of the midgut,” Micron, vol. 41, no. 3, pp. 239–246, 2010. View at: Publisher Site | Google Scholar
  48. D. G. Perez and C. S. Fontanetti, “Assessment of the toxic Potential of sewage sludge in the Midgut of the Diplopod Rhinocricus padbergi,” Water, Air and Soil Pollution, vol. 218, no. 1–4, pp. 1–8, 2010. View at: Publisher Site | Google Scholar
  49. L. J. Cole, D. I. McCracken, G. N. Foster, and M. N. Aitken, “Using Collembola to assess the risks of applying metal-rich sewage sludge to agricultural land in Western Scotland,” Agriculture, Ecosystems and Environment, vol. 83, no. 1-2, pp. 177–189, 2001. View at: Publisher Site | Google Scholar
  50. P. Andrés and X. Domene, “Ecotoxicological and fertilizing effects of dewatered, composted and dry sewage sludge on soil mesofauna: a TME experiment,” Ecotoxicology, vol. 14, no. 5, pp. 545–557, 2005. View at: Publisher Site | Google Scholar
  51. T. R. Meyers and J. D. Hendricks, “Histopathology,” in Fundamental of Aquatic Toxicology: Methods and Applications, G. M. Rand and S. R. Petrocelli, Eds., pp. 283–331, Washington, DC, USA, 1985. View at: Google Scholar
  52. H. R. Köhler and R. Triebskorn, “Assessment of the cytotoxic impact of heavy metals on soil invertebrates using a protocol integrating qualitative and quantitative components,” Biomarkers, vol. 3, no. 2, pp. 109–127, 1998. View at: Publisher Site | Google Scholar
  53. R. Triebskorn, H. R. Köhler, T. Zanh et al., “Invertebrate cells as targets for hazardous substances,” Zeitschfirt fuer Angewandte Zoologie, vol. 78, pp. 277–287, 1991. View at: Google Scholar
  54. R. A. Triebskorn, I. F. Henderson, and A. P. Martin, “Detection of iron in tissues from slugs (Deroceras reticulatum Muller) after ingestion of iron chelates, by means of energy-filtering transmission electron microscopy (EFTEM),” Pesticide Science, vol. 55, no. 1, pp. 55–61, 1999. View at: Google Scholar
  55. C. S. Fontanetti, C. A. Christofoletti, T. G. Pinheiro, T. S. Souza, and J. Pedro-Escher, “Microscopy as a tool in toxicological evaluations,” in Microscopy: Science, Technology, Applications and Education, A. Méndez-Vilas and J. Diaz, Eds., pp. 1001–1007, Formatex Research Center, Badajoz, Spain, 2010. View at: Google Scholar
  56. V. Nero, A. Farwell, A. Lister et al., “Gill and liver histopathological changes in yellow perch (Perca flavescens) and goldfish (Carassius auratus) exposed to oil sands process-affected water,” Ecotoxicology and Environmental Safety, vol. 63, no. 3, pp. 365–377, 2006. View at: Publisher Site | Google Scholar
  57. H. R. Köhler, “Localization of metals in cells of saprophagous soil arthropods (Isopoda, Diplopoda, Collembola),” Microscopy Research and Technique, vol. 56, no. 5, pp. 393–401, 2002. View at: Publisher Site | Google Scholar

Copyright © 2012 Cintya Ap. Christofoletti et al. This is an open access article distributed under the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.

More related articles

 PDF Download Citation Citation
 Download other formatsMore
 Order printed copiesOrder

Related articles

Article of the Year Award: Outstanding research contributions of 2020, as selected by our Chief Editors. Read the winning articles.