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Brazilian Journal of Microbiology

Print version ISSN 1517-8382

Braz. J. Microbiol. vol.42 no.3 São Paulo July/Sept. 2011

http://dx.doi.org/10.1590/S1517-83822011000300004 

ENVIRONMENTAL MICROBIOLOGY

 

Microbial activity, arbuscular mycorrhizal fungi and inoculation of woody plants in lead contaminated soil

 

 

Graziella S. GattaiI; Sônia V. PereiraI; Cynthia M. C. CostaII; Cláudia E. P. LimaIII,*; Leonor C. MaiaIII

IInstituto de Tecnologia de Pernambuco, Laboratório de Biotecnologia Ambiental, Recife, PE, Brasil
IIUniversidade Federal Rural de Pernambuco, Recife, PE, Brasil
IIIUniversidade Federal de Pernambuco, Departamento de Micologia, Recife, PE, Brasil

 

 


ABSTRACT

The goals of this study were to evaluate the microbial activity, arbuscular mycorrhizal fungi and inoculation of woody plants (Caesalpinia ferrea, Mimosa tenuiflora and Erythrina velutina) in lead contaminated soil from the semi-arid region of northeastern of Brazil (Belo Jardim, Pernambuco). Dilutions were prepared by adding lead contaminated soil (270 mg Kg-1) to uncontaminated soil (37 mg Pb Kg soil-1) in the proportions of 7.5%, 15%, and 30% (v:v). The increase of lead contamination in the soil negatively influenced the amount of carbon in the microbial biomass of the samples from both the dry and rainy seasons and the metabolic quotient only differed between the collection seasons in the 30% contaminated soil. The average value of the acid phosphatase activity in the dry season was 2.3 times higher than observed during the rainy season. There was no significant difference in the number of glomerospores observed between soils and periods studied. The most probable number of infective propagules was reduced for both seasons due to the excess lead in soil. The mycorrhizal colonization rate was reduced for the three plant species assayed. The inoculation with arbuscular mycorrhizal fungi benefited the growth of Erythrina velutina in lead contaminated soil.

Key words: AMF, contaminated soil, heavy metals, mycorrhizae, semi-arid.


 

 

INTRODUCTION

Over the last few decades industrial activities have increased the level of pollution in the biosphere, including soils, with a negative impact on the environment (31). Among these pollutants, heavy metals are considered the most relevant causes of soil contamination (11).

The effect of soil contamination by metals is reflected in the nutrient cycle, which can be determined by estimating the level of microbial biomass, CO2 emission, enzymatic activity and organic matter decomposition (2,9). A plant's response to contamination by metals varies depending to the contamination level, soil type, and the diversity of microorganisms and plants that influence the soil processes (6).

Among the microorganisms common to many soils, arbuscular mycorrhizal fungi (AMF), which are obligate symbionts, can increase the survival rate of certain plants by helping them take up nutrients and water and promoting healthy roots (30). They can also potentially help in the recovery of heavy metals from polluted environments (18).

Even though the toxicity caused by metals can be attenuated by AMF (19,25), healthy development of plants in contaminated soil depends on other factors, such as the intensity of the contamination, bioavailability of a particular metal to the roots, and the plants ability to absorb and accumulate this metal in their leaves (7).

Considering the importance of AMF and the need to establish strategies to rehabilitate contaminated areas, the goals of this study were to evaluate the microbial activity, arbuscular mycorrhizal fungi and inoculation of woody plants in lead-contaminated soil found in the semi-arid region of northeastern Brazil.

 

MATERIALS AND METHODS

The soil samples were collected (0-20 cm deep) in the dry season and rainy season at two sites in the municipality of Belo Jardim, Pernambuco (08º20'08" S, 36º25'27" W). One site contained lead-contaminated soil (270 mg Kg-1), derived from solid waste from a mechanical metal industry, and the other site had no contamination (37 mg Pb Kg-1). From each site, eight subsamples were collected to make two samples, one called non-contaminated soil (NCS) and the other called contaminated soil (CS). Dilutions of the soil samples were prepared by adding the contaminated soil to the natural soil to obtain the following contamination proportions: 0%, used as control, 7.5%, 15%, and 30% (v:v).

The experiments were conducted in the greenhouse of the Departamento de Micologia at the Universidade Federal de Pernambuco. Physicochemical analyses of the samples were made in the Laboratório de Biotecnologia Ambiental at the Instituto de Tecnologia de Pernambuco (ITEP) and the Instituto Agronômico de Pernambuco (IPA). The soil (a sandy clay loam), from both collection periods and at each contamination proportion, was chemically analyzed. The method of acid leaching was in accordance with the standards issued by the Associação Brasileira de Normas Técnicas (3). This method was used to analyze the lead in the soil with a coupled plasma-atomic emission spectrometer.

Microbial activity in the soil

The microbial activity was evaluated by the following analyses: (a) carbon of the microbial biomass, by the fumigation-extraction method (15,28); (b) basal respiration (13); (c) metabolic quotient (qCO2); and (d) acid phosphatase activity (26). These analyses were replicated five times for each soil treatment (0%, 7.5%, 15%, and 30%), and samples collected during the dry and rainy seasons.

Most probable number (MPN) of infective propagules and arbuscular mycorrhizal fungi (AMF) spores in the soil

Samples of NCS and CS, collected in the dry and rainy seasons, were used to estimate the MPN of infective propagules and spores of AMF (glomerospores). Maize (Zea mays L.) seedlings were used as hosts and autoclaved sand was used to dilute the original inocula (8). The presence of typical AMF forming structures was investigated after 30 days in roots cleared and stained with Trypan blue (24). Glomerospores were extracted from NCS and CS samples using the wet sieving method (10) and then centrifuged in water and saccharose (14), with three replicates per treatment.

AMF inoculation of wood plants in contaminated soil

Seeds from the following plants were used in this study: Caesalpinia ferrea C. Martius and Mimosa tenuiflora (Wild.) Poir., obtained from IPA; and Erythrina velutina Wild., obtained from the Empresa Brasileira de Pesquisa Agropecuária - Embrapa Semi-Árido. The seeds were disinfected with sodium hypochloride (0.05%) and seeded in trays with NCS soil. After growth of the first true leaves, the plantlets were transferred to plastic bags containing 2 kg of substrate each.

Plantlets of M. tenuiflora, C. ferrea and E. velutina were inoculated at the root region with 100 glomerospores extracted from NCS and from the 15% contaminated soil. After 90 days the plantlets were evaluated by measuring the height, stem diameter and dry weight of the aerial parts. Mycorrhizal colonization was observed on roots stained with Trypan Blue in lactoglycerol (24) and quantified by the grid-line intersect method (12). The experimental design was randomly outlined in 3 × 2 × 2 factorial, with 3 plant species, 2 inoculation treatments (with and without AMF) and 2 substrates (NCS and 15% contaminated soil), in five replicates.

The data were analyzed using analysis of variance and the means were compared by Tukey's test (P < 0.05).

 

RESULTS AND DISCUSSION

Starting at 7.5% contamination, the lead levels were above the acceptable level (300 mg kg-1 and 50 mg kg-1) for alkali and acidic soils, respectively (5). With a concentration above 58.6 mg kg Pb-1, the soil's pH (±4.9) might have helped make the metals available and to reduce the carbon and nitrogen levels of the microbial biomass (16). In general, the nutrients (P, Ca, Mg and Al) were present in higher concentrations in the rainy seasons, regardless of the level of contamination, which resulted in increased microbial activity during this period (Table 1).

The increase of lead contamination in the soil negatively influenced the amount of carbon of the microbial biomass in the samples from both the dry and rainy seasons (Figure 1). It has been found that the microbial biomass activity of soil is negatively related to heavy metal concentration and positively related to the amount of organic matter (29). This reduction suggests that excess lead in soil is harmful to microorganisms, regardless of the amount of water in the soil. Physical limitations, such as lack of water, low aeration and porosity of soils, influence the biological communities that live in them, and when there is low water potential, most soil microorganisms become inactive. On the other hand, under the same stressful conditions, certain microorganisms can increase their sporulation rate in an attempt to increase the chances of survival during a dry period (22). In fact, during the rainy season, the amount of carbon of the microbial biomass was significantly higher (232 µg C g soil-1) compared to the samples from the dry season (70 µg C g soil-1), which could be due to the higher activity of the microorganisms and consequently the higher accumulation of organic matter in the substrates (Table 1).

The basal respiration was significantly inhibited by the increase of the soil contaminant in the samples collected during the rainy season, and was different when compared to the natural soil samples (Figure 2). Liao et al. (18) found that increasing heavy metal concentrations of Cu and Cd reduced basal respiration, an activity that is related to the increase of organic matter, which is responsible for complexation of available metals.

The metabolic quotient (qCO2) estimated in the soil only differed between the collection seasons in the 30% contaminated soil. During the dry season, the highest qCO2 rates were recorded with increasing proportions of lead-contaminated soil (Figure 3), which indicates that the ecosystem was under stress. These results show that microbial populations invest most of their energy for maintenance, a typical condition of disturbed environments (21).

In general, the average value of the acid phosphatase activity in the dry season (3.14 µg p-np g soil-1) was 2.3 times higher than observed during the rainy season (1.33 µg p-np g soil-1) (Figure 4a). The NCS (2 µg p-np g soil-1) differed only from the 7.5% contamination sample (2.4 µg p-np g soil-1), though there was a tendency towards reduced activity when the proportion of contamination in the soil was increased (15% and 30%) (Figure 4b). These results suggest that if there is up to 80.3 mg kg-1 of lead in the soil (7.5%), the activity of acid phosphatase can be induced. However, above this level the activity was reduced, indicating the deleterious effect of lead on the soil microbiota. The activity of acid phosphatase was positively related to the pH and negatively related to the phosphorous available in the soil. The enzymatic activity is directly related to the physical and chemical properties of the soil, especially to the phosphatase activity, which plays an important role in the mineralization of phosphorous, related in this case to the total amounts of P found in the soil (11).

The number of glomerospores did not differ significantly between NCS and CS in the rainy and dry seasons. However, in the CS the MPN of infective propagules was drastically reduced in both the rainy and dry seasons due to the excess lead (270 mg Kg-1) (Table 2). These data corroborate studies showing that the number of glomerospores, the spore germination of AMF and mycorrhizal infectivity are directly affected by the concentration and kind of metals in the soil (18). In copper-contaminated soil (484 mg dm-3), the spore production of AMF was negatively influenced by higher contamination levels (75% and 100%). However, a lower contamination level (25%) favored sporulation (20). Trap cultures are being kept in a greenhouse in an attempt to recover as many glomerospores and identify species of AMF in the region (data not shown). Studies in the Amazon region have demonstrated that the spore production of AMF was more abundant in trap cultures from land uses under interference than in the pristine forest ecosystem (17).

The colonization rate of AMF was below 10% for the three plant species assayed in the NCS and 15% contaminated soil. E. veluntina had the lowest colonization rate (1.5%) in both soils and the rate declined in the roots of both M. tenuiflora (6.5% to 2.7%) and C. ferrea (8.7 % to 6.0%) when the proportion of contaminated soil was increased. However, this reduction was not significant. This shows that in general a high concentration of metals interferes in mycorrhizal association. The Cd toxicity to Trema micrantha (L.) Blum was evaluated by Soares et al. (25). They found that the Cd inhibited the colonization of AMF even at the lowest tested concentration (5 fmol L-1). Low levels of root colonization by AMF can be a result of lead contamination of the soil. The metal can be toxic to fungi, reducing glomerospore germination, growth of mycelium and mycorrhizal colonization (23).

The growth of M. tenuiflora and E. velutina was not influenced by the addition of lead in the substrate, while C. ferrea appeared to be sensitive height to 15% contamination (Table 3). This can be explained by the excess lead in the soil solution, indicating an inhibitory effect. In spite of the low colonization rates for the three plant species, only C. ferrea and E. velutina responded to the inoculation in some of the growth parameters. In E. velutina, the stem diameter of the inoculated plants differed from the non-inoculated plants for both soil treatments (0% and 15% contamination). In addition, the amount of dry matter was higher in the colonized plants, especially in the 15% contamination treatment. Plantlets of C. ferrea also showed a significant difference in height when grown in non-contaminated soil.

In a study by Trannin et al. (27), the cultivation of three woody plant species (Acacia mangium, Enterolobium contortisiliquum and Sesbania virgata) in heavy metal contaminated soil had a negative effect on the growth, dry weight of the aerial parts, height, and stem diameter of these plants. These authors observed a phytotoxic effect of the metals on the three species for soils with 15% contamination. Plantlets of Leucaena leucocephala (Lam.) de Wit cultivated in three soils in the caatinga (which was preserved, without the superficial layer, and contaminated with copper effluent from mining) showed lower growth in the copper contaminated treatment, due to the higher absorption of this metal by the roots (20). In another study using soybean plants, the addition of Pb to the soil reduced the growth of the plants with mycorrhizae, directly influencing the production of dry matter (1).

Recent studies in contaminated environments have shown there is a strong reduction in growth in colonized and non-colonized plants as the contamination level increases (1,20). It has also been found that AMF vary from tolerant to very sensitive when they are growing in soil with heavy metals (4) and that plant development depends on the contamination level and the type of heavy metal present. The results of this work confirm these observations and show that in lead-contaminated soil only E. velutina responded to inoculation.

 

CONCLUSIONS

The microbial activity in the semi-arid region of northeastern Brazil (Belo Jardim, Pernambuco) is negatively affected by lead contamination in the soil.

The activity of acid phosphatase in the soil from the semi-arid region can be induced when there is up to 80.3 mg kg-1 of lead in the soil.

Mycorrhizal infectivity in soil from the semi-arid region is directly affected by the concentration of lead in the soil.

Inoculation with arbuscular mycorrhizal fungi benefits the growth of Erythrina velutina in soil with moderate lead contamination levels (up to 80.3 mg Pb Kg soil-1).

 

ACKNOWLEDGMENTS

We would like to thank the Instituto de Tecnologia de Pernambuco (ITEP) for the support in analyzing the soils, Instituto Agronômico de Pernambuco (IPA) and the Empresa Brasileira de Pesquisa Agropecuária - Embrapa Semi-Árido for providing the seeds used in this study, and CAPES and CNPq for providing grants to G. Gattai, C. Lima and L. Maia.

 

REFERENCES

1. Andrade, S.A.L.; Abreu, C.A.; Abreu, M.F.; Silveira, A.P.D. (2003). Interação de chumbo, da saturação por bases e de micorriza arbuscular no crescimento e nutrição mineral da soja. Rev. Bras. Cienc. Solo. 27,945-954.         [ Links ]

2. Andrade, S.A.L.; Silveira, A.P.D. (2004). Biomassa e atividade microbianas do solo sob influência de chumbo e da rizosfera da soja micorrizada. Pesqui. Agropecu. Bras. 39,1191-1198.         [ Links ]

3. Associação Brasileira de Normas Técnicas. (1987). Fórum Nacional de Normalização NBR 10005. Lixiviação de resíduos. Rio de Janeiro         [ Links ]

4. Carneiro, M.A.C.; Siqueira, J.O.; Moreira, F. M. S. (2002). Comportamento de espécies herbáceas em misturas de solo com diferentes graus de contaminação com metais pesados. Pesqui. Agropecu. Bras. 37,1629-1638.         [ Links ]

5. Companhia de Saneamento do Paraná. (1997). Plano anual de operação e manutenção de esgotamento sanitário. Maringá: Sanepar-Maringá         [ Links ].

6. Dick, R.P. (1997). Soil enzyme activities as integrative indicators of soil health. In: Pankhurst, C.E.; Doube, B.M.; Gupta, V.V.S.R. (eds.). Biological Indicators of Soil Health. USA: Cab International, p. 21-156.         [ Links ]

7. Ernest, W.H.O. (1996). Biovailability of heavy metals and decontamination of soils by plants. Appl. Geochem. 11,163-167.         [ Links ]

8. Feldmann, F.; Idczak, E. (1994). Inoculum production of vesiculararbuscular mycorrhizal fungi for use in tropical nurseries. In: Norris, J.R.; Read, D.J.; Varma, A.K. (eds.). Techniques for Mycorrhizal Research. London: Academic Press, p. 799-817.         [ Links ]

9. García, C.; Hernández, T. (1997). Biological and Biochemical indicators in derelict soils subject to erosion. Soil Biol. Biochem. 29,171-177.         [ Links ]

10. Gerdemann, J.W.; Nicolson, T.H. (1963). Spores of mycorrhizal Endogone species extracted from soil by wet sieving and decanting. T. Brit. Mycol. Soc,. 235-244.         [ Links ]

11. Gianfreda, L.; Rao, M.A.; Piotrowska, A.; Palumbo, G.; Colombo, C. (2005). Soil enzyme activity as affected by anthropogenic alterations: intensive agricultural practices and organic pollution. Sci. Total Environ. 341,265-279.         [ Links ]

12. Giovannetti, M.; Mosse, B. (1980). An evaluation of techniques for measuring vesicular arbuscular mycorrhizal infection in roots. New Phytol. 84,489-500.         [ Links ]

13. Grisi, B.M. (1978). Método químico de medição da respiração edáfica: alguns aspectos técnicos. Cienc Cult. 30,82-88.         [ Links ]

14. Jenkins, W. R. (1964). A rapid centrifugal-flotation technique for separating nematodes from soil. Plant Dis. Rep. 48,692.         [ Links ]

15. Joergensen, R.G. (1996). The fumigation-extraction method to estimate soil microbial biomass: calibration of the kEC value. Soil Biol Biochem, 28,25-31.         [ Links ]

16. Khan, M.; Scullion, J. (2002). Effects of metal (Cd, Cu, Ni, Pb or Zn) enrichment of sewage-sludge on soil micro-organisms and their activities. Appl. Soil Ecol. 20,145-155.         [ Links ]

17. Leal, P.L.; Stürmer, S.L.; Siqueira, J.O. (2009). Occurrence and diversity of arbuscular mycorrhizal fungi in trap cultures from soils under different land use systems in the Amazon, Brazil. Braz. J. Microbiol. 40,111-121.         [ Links ]

18. Liao, J.P.; Lin, X.G.; Cao, Z.H.; Shi, Y.Q.; Wong, M.H. (2003). Interactions between Arbuscular Mycorrhizae and Heavy Metals under Sand Culture Experiment. Chemosphere 50,847-853.         [ Links ]

19. Lins, C.E.L.; Cavalcante, U.M.T.; Sampaio, E.V.S.B.; Messias, A.S.; Maia, L.C. (2006). Growth of mycorrhized seedlings of Leucaena leucocephala (Lam.) de Wit. in a copper contaminated soil. Appl. Soil Ecol. 31,181-185.         [ Links ]

20. Lins, C.E.L.; Maia, L.C.; Cavalcante, U.M.T.; Sampaio, E.V.S.B. (2007). Efeito de fungos micorrízicos arbusculares no crescimento de mudas de Leucaena leucocephala (Lam.) de Wit. em solos de caatinga sob impacto de mineração de cobre. Rev. Árvore 31,355-363.         [ Links ]

21. Luna, R.G.; Coutinho, H.D.M.; Grisi, B. M. (2008). Evaluation of pasture soil productivity in the semi-arid zone of Brazil by microbial analyses. Braz. J. Microbiol. 39,409-413.         [ Links ]

22. Moreira, F.M.S.; Siqueira, J.O. (2006). Microbiologia e Bioquímica do Solo. Lavras: Editora UFLA.         [ Links ]

23. Orlowska, E.; Ryszka, P.; Jurkiewicz, A.; Turnau, K. (2005). Effectiveness of arbuscular mycorrizal fungal (AMF) strains in colonization of plants involved in phytostabilisation of zinc wastes. Geoderma. 129,92-98.         [ Links ]

24. Phillips, J.M.; Hayman, D.S. (1970). Improved procedures for clearing roots and staining parasitic and vesicular-arbuscular mycorrhizal fungi for rapid assessement of infection. T. Brit. Mycol. Soc. 55,158-161.         [ Links ]

25. Soares, C.R.F.S.; Siqueira, J.O.; Carvalho, J.G.; Guilherme, L.R.G. (2007). Nutrição fosfática e micorriza arbuscular na redução da toxicidade de cádmio em trema [Trema micrantha (L.) Blum.]. Rev Árvore 31,783-792.         [ Links ]

26. Tabatabai, M.A.; Bremner, J.M. (1969). Use of p-nitrophenyl phosphate for assay of soil phosphatase activity. Soil Biol. Biochem. 1,301-307.         [ Links ]

27. Trannin, I.C.B.; Moreira, F.M.S.; Siqueira, J.O. (2001). Crescimento e nodulação de Acácia mangium, Enterolobium contortisiliquum e Sesbasnia virgata em solo contaminado com metais pesados. Rev. Bras. Cienc. Solo 25,743-753.         [ Links ]

28. Vance, E. D.; Brookes, P. C.; Jenkinson, D. S. (1987). An extraction

29. method for measuring soil microbial biomass C. Soil Biol. Biochem. 19,703-707.

30. Vásquez-Murrieta, M.S.; Migueles-Garduno, I.; Franco-Hernández, O.; Govaerts, B.; Dendooven, L. (2006). C and N mineralization and microbial biomass in heavy-metal contaminated soil. Eur. J. Soil Biol. 42,89-98.         [ Links ]

31. Vogel-Mikus, K.; Pongrac, P.; Kump, P.; Necemer, M.; Regvar, M. (2006). Colonization of a Zn, Cd and Pb hyperaccumulator Thlaspi praecox Wulfen with indigenous arbuscular mycorrhizal fungal mixture induces changes in heavy metal and uptake. Environ. Pollut. 139,362-371.         [ Links ]

32. Yanqun, Z.; Yuan, L.; Schvartz, C.; Langlade, L.; Fan, L. (2004). Accumulation of Pb, Cd, Cu e Zn in plants and hyperaccumulator choice in lamping lead-zinc mine area, China. Environ. Int. 30,567-576.         [ Links ]

 

 

Submitted: July 03, 2010; Returned to authors for corrections: November 03, 2010; Approved: January 31, 2011.

 

 

* Corresponding Author. Mailing address: Departamento de Micologia, Universidade Federal de Pernambuco. Av. Prof. Nelson Chaves s/n, Cidade Universitária. 50670-420, Recife, PE, Brasil.; Tel.: +55 81 2126 8865 Fax: +55 81 21268482.; E-mail: claudiaeplima@gmail.com

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