Changes in chemical attributes of a Fluvent cultivated with castor bean and irrigated with wastewater

Alterações nos atributos químicos de um Neossolo Flúvico cultivado com mamoneira e irrigado com água residuária

SOIL, WATER AND PLANT MANAGEMENT

Changes in chemical attributes of a Fluvent cultivated with castor bean and irrigated with wastewater

Alterações nos atributos químicos de um Neossolo Flúvico cultivado com mamoneira e irrigado com água residuária

Aurelir N. Barreto^I; Joab J. V. R. do Nascimento^II; Everaldo P. de Medeiros^III; Janiny A. da Nóbrega^IV; Jose R. C. Bezerra^V

^IEmbrapa Algodão. Rua Oswaldo Cruz, 1143, Centenário, CP 174, CEP 58428-095, Campina Grande, PB. In memoriam. Fone:(83) 3182-4300

IIDAIC/IFPE. Av. Prof. Luiz Freire, nº 500, Cidade Universitária, CEP 50070-540, Recife, PE. Fone: (81) 2125-1600. E-mail: [e-mail]

IIIEmbrapa Algodão. Rua Oswaldo Cruz, 1143, Centenário, CP 174, CEP 58428-095, Campina Grande, PB. Fone:(83) 3182-4300. E-mail: [e-mail]

^IVUAEA/UFCG. Rua Aprígio Veloso, 882, Bairro Universitário, CEP 58429-900, Campina Grande, PB. Fone: (83) 9654-4768. E-mail: [e-mail]

^VEmbrapa Algodão. Rua Oswaldo Cruz, 1143, Centenário, CP 174, CEP 58428-095, Campina Grande, PB. Fone:(83) 3182-4300. E-mail: [e-mail]

ABSTRACT

Agricultural use of wastewater is an alternative to increase water availability, especially in semiarid regions. However, it may cause undesirable chemical changes in the soil. The aim of this study was to evaluate the influence of wastewater irrigation and castor bean (Ricinus communis L.) cultivation on the chemical attributes of a Fluvic Neosol. The experimental design was in a randomized block, in split-plot scheme, where the main plots were represented by the treatments of irrigation water and castor bean cultivation, and the subplots were the soil layers, with three replications. The treatments were T1 – wastewater irrigation + castor bean cultivation ; T2 – mixture of supply water and wastewater (1:1 ratio) + castor bean cultivation; T3 – supply water irrigation + castor bean cultivation ; and T4 – wastewater application, without castor bean cultivation. The depths of soil layers were 0-10, 10-20, 20-30, 30-40, and 40-50 cm. At the end of study, the content of phosphorus, calcium, potassium, and organic matter increased mainly in the upper layers, and sodium increased in the deeper layers in the wastewater treatments, in comparison to the supply water irrigation. In T4, the disposal of wastewater increased the concentration of magnesium. The pH values, iron and zinc concentration did not statistically differ in the treatments.

Key words: reuse, nutrients, effluent, water management, Ricinus communis

RESUMO

A utilização de água residuária na agricultura é uma alternativa de aumento da disponibilidade hídrica, sobretudo nas regiões semiáridas passíveis, no entanto, de causarem alterações químicas indesejáveis no solo. Objetivou-se, neste trabalho, avaliar os efeitos da aplicação de diferentes manejos de água nas características químicas de um Neossolo Flúvico cultivado com mamoneira (Ricinus communis L.). Instalou-se um experimento em blocos casualizados com parcelas subdivididas enquanto as parcelas continham os seguintes tipos de manejo de água (T1 - irrigação com água residuária + cultivo de mamoneira; T2 - irrigação com uma mistura de água residuária e água de abastecimento, na proporção 1:1 (v/v) + cultivo de mamoneira; T3 - irrigação com água de abastecimento,+ cultivo da mamoneira; T4 - aplicação de água residuária, sem cultivo de mamoneira) e nas subparcelas as faixas de profundidade (0-10; 10-20; 20-30; 30-40 e 40-50 cm), com três repetições. Após a aplicação da água residuária no solo os teores de fósforo, cálcio, potássio e matéria orgânica, principalmente na camada superficial, e sódio, em profundidade, aumentaram significativamente, em comparação com a aplicação de água de abastecimento. No solo sem cultivo a disposição de água residuária aumentou a concentração de magnésio. Os valores de pH, ferro e zinco não se alteraram.

Palavras-chave: reúso, nutrientes, efluente, manejo de água, Ricinus communis

INTRODUCTION

Water scarcity is a worldwide concern, which is worsened by the increasing demand for various uses (Corwin & Bradford, 2008). In spite of 18% of total world freshwater being located in Brazil, there are many national problems of water supply, mainly due to the heterogeneous geographical water distribution and inadequate management, that causes pollution, wastage, and overuse.

The use of wastewater for irrigation is a viable option to reduce the use of water resources and to increase the supply of quality water for more restrictive uses, such as drinking water (Tozé, 2006). Besides being a source of water, the wastewaster contains nutrients, organic matter, and soil conditioning agents, which promote the establishment of crops, and increase their productivity (Fonseca et al., 2007).

The organic matter in wastewater can improve soil aeration, infiltration rate, water storage, cation exchange capacity (CEC), as well as decrease the potential for soil erosion and increase the population of organisms which promotes plant growth (Tozé, 2006; Corwin & Bradford, 2008; Arienzo et al., 2009). Moreover, this practice is an effective method to control pollution, avoiding the discharge of effluents into water bodies (Tozé, 2006).

Despite the benefits of wastewater in agriculture, its application can create environmental problems, as a consequence of some chemical and biological undesirable constituents (Tozé, 2006; Rusan et al., 2007). It has been observed under Brazilian soil and climatic conditions that this practice may affect the content of macro and micronutrients, organic matter, heavy metals, sodium, exchangeable sodium percentage (ESP), pH, and CEC (Fonseca et al., 2007; Herpin et al., 2007; Duarte et al., 2008; Leal et al., 2009 a,b; Leal et al., 2010).

The magnitude of changes in soil chemical attributes depends mainly on local conditions, such as soil type, depth range, quality and quantity of used wastewaster in the system, and the kind of grown plant species (Corwin & Bradford, 2008; Kiziloglu et al., 2008; Xu et al., 2010; Liang et al., 2010; Leal et al., 2010). These changes may result in significant impacts in the soil quality (Fonseca et al., 2005; Herpin et al., 2007), or may not (Varallo et al., 2010; Duan et al., 2010). Thus, the soil chemical attributes must be continuously monitored (Leal et al., 2009b). Fonseca et al. (2007) and Herpin et al. (2007) suggest that studies on the environmental impacts of wastewater disposal in soil, in different soil types and different cropping systems, under various climatic conditions, must be conducted to evaluate the environmental and economic impacts. Measurements of this kind allow the establishment of recommendations of use of wastewater, especially in Brazilian agroecosystems, in which this kind of information is still very rare.

The aim of this study was to evaluate the changes in the chemical attributes of several layers of a Fluvic Neosol under castor bean cultivation, in drainage lysimeters with different wastewater management strategies, under Brazilian semiarid conditions.

MATERIAL AND METHODS

The experiment was carried out in Campina Grande, Paraiba State, Brazil (7º 13' 50" S, 35º 52' 52" W). The study was conducted in 12 drainage monolithic lysimeters, with the total depth of 1.0 m and diameter of 0.70 m, built on the left bank of Bodocongó stream (7º 14' 25" S, 35º 55'14" W, elevation of 501 m). The lysimeters were replaced to the experimental area of the Federal University of Campina Grande (UFCG) (7º 12' 52" S,35º 54' 25" W, elevation of 528 m).

The soil is a Eutrophic Fluvic Neosol (EMBRAPA, 2006), sandy loam, where castor bean was grown. The hydro-physical (Table 1) and chemical (Table 2) analyses of the soil before the experiment were carried out following methodologies recommended by EMBRAPA (1997).

The wastewater used in the experiment came from a stream that receives contributions from sewers and passes through the experimental area of the Academic Unit of Agricultural Engineering of UFCG. The wastewater was filtered with a nylon sieve (Φ = 2.0 mm) at the point of capture to remove coarse solids. The potable water came from the public water supply system of Campina Grande. Analyses of potable water and wastewater were performed according to methodologies recommended by APHA (1999) and the results are presented in Table 3.

Five seeds of castor bean (Ricinus communis L.) CV BRS Energy were sown in the lysimeters in the first fortnight of September 2007 and 15 days after germination, thinning was done, leaving only one plant per lysimeter. Irrigation was applied for 120 days until it reached a total of 1,000 mm of potable water and/or wastewater. Afterwards, irrigation was stopped because the castor bean had completed the development cycle.

The volumetric water content in the 0-60 cm layers was monitored every 2 days using a capacitance probe (model Diviner 2000). Irrigation was performed with manual randomized application of water, based on water demand of the crop.

The experiment was arranged in a completely randomized block design, in a split-plot scheme, with three replications. The treatments consisted of: T1 – Wastewater irrigation + castor bean cultivation; T2 – Wastewater and supply water mixture (1:1 proportion) + castor bean; cultivation T3 – Supply water irrigation + castor bean cultivation ; and T4 – wastewater application, without castor bean cultivation. The analysed depths were considered as the subplots (0-10, 10-20, 20-30, 30-40, and 40-50 cm). No fertilizer was applied.

Soil samples were collected in September 2007 (initial soil condition, prior to castor bean planting, and January 2008 (after 120 days of irrigation, at the time of harvest). Samples were collected at 0-10, 10-20, 20-30, 30-40 and 40-50 cm depths.

After air-drying, the soil samples were passed through a 2 mm seive. The soil analysis were carried out as described in EMBRAPA (1997). pH was determined in 1:2,5 soil water suspension. Organic matter determination was carried out as described by Walkley-Black method. Calcium and magnesium were extracted using KCl 1.0 mol L^-1 and titration by EDTA. Potassium and sodium were extracted using HCl 0.05 mol L^-1 and determined by flame photometry. Potential acidity was determined by means of 0.5 mol L^-1 calcium acetate solutions at pH 7.0. Phosphorus was extracted using HCl 0.05 mol L^-1 and was determined by colorimetry. The concentrations of available iron, manganese, copper, and zinc were determined by Mehlich-1 method.

The results of soil data were submitted to variance analysis. The statistical analysis were performed for each parameter and the variables showing results significantly different in the F-test (P < 0.05) were submitted to mean comparison by Tukey's test (P < 0.05).

RESULTS AND DISCUSSION

The higher Ca²⁺ concentrations (treatment means) were observed in T1, which can be explained by the combined action of addition via wastewater (Kiziloglu et al., 2008) and castor bean absorption by evapotranspiration, showing a statistical difference in comparison to other treatments (Table 4).

Although castor beans can absorb significant amounts of Ca²⁺ when grown in the presence of sewage sludge (Chiaradia et al., 2009), this nutrient is usually present in large amounts in wastewater from households, reaching in some cases concentrations higher than Na⁺, as observed in other studies (Medeiros et al., 2007; Sandri et al., 2009). These high levels in wastewater may lead to accumulation, even under crop cultivation , as found by Herpin et al. (2007).

In general lines, calcium was accumulated in the topsoil. There is a reduction of calcium concentration in the 10 cm depth below topsoil. The release of this cation by organic matter mineralization was retained in the surface layer (Table 4), and it may explain its higher concentration in this depth. The increase of Ca²⁺ in this layer, as result of wastewater irrigation, was reported by Leal et al. (2009a). On the other hand, Herpin et al. (2007) found an increase with depth, involving leaching, plant uptake and reaction of Ca²⁺ with carbonates and sulfates, which were present in the applied effluent.

The wastewater management had significant effect on the concentration of Mg²⁺ in the soil profile (Table 4), with higher values for T4. In T1, despite receiving the same water as T4, the added Mg²⁺ from the wastewater, usually present in low concentrations (Medeiros et al., 2007; Sandri et al., 2009; Leal et al., 2009a), was probably absorbed by the castor bean plants, since this nutrient is the 5^th most required nutrient for castor bean crop (Chiaradia et al., 2009). Supply water (T3) did not change the exchangeable magnesium neither calcium concentrations.

The Mg²⁺ absorption by plants can decrease its levels in the soil, even under wastewater irrigation, as verified by Fonseca et al. (2005) for Zea mays. Also, wastewater often contains solutes that can form magnesium precipitates, decreasing its availability. As there was no Mg²⁺ absorption in T4, this cation tended to increase its soil concentration. Increments in Mg²⁺ concentration due to the wastewater application were also observed by Sandri et al. (2009). However, Kiziloglu et al. (2008), Leal et al. (2009a), and Varallo et al. (2010) found no significant effect of wastewater irrigation on Mg²⁺ content in soil.

Only in T4, the deeper the soil profile, the higher was Mg²⁺ concentration, because Mg²⁺ was more subjected to leaching due to the absence of crop. In T1, T2, and T3, there were no changes in Mg²⁺ concentration with the depth. These results corroborate with Leal et al. (2009a) and Herpin et al. (2007) information, who detected no changes in the magnesium levels between layers from 10 cm to 40 cm in sugarcane and coffee crops, respectively. Sandri et al. (2009) found no differences between the Mg²⁺ concentrations in the depth of 0-10 and 10-20 cm for lettuce cultivation.

The wastewater irrigation increased Na⁺ concentration across the profile, when compared with baseline values (Tables 2 and 4). Unlike other cations, Na⁺ has a low affinity for soil exchange complex, mainly occurring in the soil solution, from where it can be leached (Leal et al., 2009a). Thus, the Na⁺ added from wastewater, usually present in high concentration (Kiziloglu et al., 2008), moves easily into the subsoil (Tarchouna et al., 2010), which justifies the increment of the cation levels as a function of the depth. Similar results were obtained by Heidarpour et al. (2007), who found accumulation of sodium in deeper layers due to leaching.

The lowest concentration in T4 is justified by the higher leaching, since there was no plant to consume part of the applied water.

Increments in Na⁺ concentration after wastewater irrigation in agricultural soils are reported in studies of short and long term durations (Fonseca et al., 2005; Leal et al., 2009a). Besides the rate of water application and Na⁺ content in the wastewater (Rusan et al., 2007), the absorption capacity of the crop (Sandri et al., 2009) and soil texture may have direct influence on the accumulation of this cation throughout the soil profile. Thus, crops with higher extraction capacity can reduce the levels of exchangeable sodium, and sandy soils tend to loose it more easily by leaching, due to reduced presence of negative charges, compared to clay soils (Sandri et al., 2009).

There was an increment in exchangeable K⁺ in the wastewater irrigated plots, compared with those receiving supply water, in the following crescent order: T2 = T3 < T1 < T4 (Table 4), that may be related to the absence of castor bean to absorb potassium in T4.

In spite of relatively low concentration of this cation in wastewater (Arienzo et al., 2009), in many studies the increment in soil exchangeable K⁺ has been reported after wastewater irrigation (Herpin et al., 2007; Heidarpour et al., 2007; Kiziloglu et al., 2008). However, these results are in disagreement with those obtained by Fonseca et al. (2005), who observed no significant effect and Varallo et al. (2010), who found a reduction in K⁺ soil concentration after wastewater disposal.

The K⁺ concentration in the surface layer (0-10 cm) of wastewater irrigated plots was significantly higher compared to the other layers. The potential for potassium accumulation in the soil for the wastewater disposal is high, due to low leaching capacity of this element (Arienzo et al., 2009). Also according to these authors, the potassium that is not absorbed by the plants is adsorbed by the soil, minimizing the leaching risk.

The much lower potassium concentration in comparison to Mg²⁺ and Ca²⁺ contents may have contributed to its accumulation, because in this condition, a preferential adsorption of K⁺ occurs in the upper layer, which may explain the lower leaching of this cation in comparison to Ca²⁺ and Mg²⁺ (Ernani et al., 2006). Heidarpour et al. (2007) irrigated bermuda grass with wastewater and verified, at the end of the experiment, a higher potassium concentration in the 0-15 cm layer, compared to 15-30 cm. The soil pH was slightly acid in all depths before the irrigation treatments (Table 2). At the end of the experiment, T1 and T4 showed average pH values above 7.0, while T2 and T3 were still below 7.0, although all treatments were similar by the Tukey's test at 0.05 probability level. A significant increment was found in pH at 0-10 and 10-20 cm of T1, T2, and T4, compared with the others layers. In T3, there was no significant difference in pH among all the layers.

Small increments in pH were observed by Leal et al. (2009a) in the soil where sugarcane was grown with treated wastewater irrigation. Moreover, no changes in this attribute were observed by Varallo et al. (2010) after application of domestic wastewater in soil columns without cultivation.

The soil pH increased in T3, in comparison to the soil before irrigation. This can be attributed to the pH of the supply water (Table 3), which was higher than 7.0 and increased soil alkalinity. In the wastewater irrigation, the pH increment in the upper layer may be related to some factors, as: (i) the presence of exchangeable cations, (ii) the alkalinity of the water, (iii) the denitrification increment, which consumes one mole of H⁺ for each mole of denitrified NO₃^-, and (iv) the chelation of Al³⁺ by accumulated organic matter on the soil surface (Fonseca et al., 2005; Fonseca et al., 2007; Silva & Mendonça, 2007). Small changes in pH (less than one unit) by the wastewater application are generally not able to directly affect the crops (Leal et al., 2009a).

The potential acidity (H + Al) significantly decreased in the soil of the wastewater irrigated plots, in comparison to those receiving supply water in the following crescent order: T4 < T1 < T2 < T3 (Table 5). The lowest values were observed in the upper layer of T1, T2, and T4, which may be related to increased levels of organic matter in this layer (Table 5), that may chelate aluminum (Silva & Mendonça, 2007). Reductions in the potential acidity have been found in soil irrigated with treated wastewater (Fonseca et al., 2005; Herpin et al., 2007; Leal et al., 2009a) and they are attributed to the increment of the exchangeable cations in the soil and the alkalinity of applied wastewater.

The wastewater irrigation affected the soil P content. The P concentrations in T1, T2, and T4 were higher after the irrigations (Tables 2 and 5). Thus, wastewater increased the P concentration in the analysed soil samples.

Certainly, the P input from wastewater was significant for the castor bean plants nutrition, decreasing the levels in soil samples from experimental units that contained this plants, since in T1 the levels were significantly lower than those of T4, despite having received only wastewater. Nevertheless, it appears that in some situations the P content in wastewater does not meet the castor bean nutritional demand, as verified by Souza et al. (2010), under field conditions in the State of Ceará, Northeastern Brazil.

The increment in soil P concentration due to the wastewater disposal is regularly observed, even in short duration experiments (Herpin et al., 2007; Kiziloglu et al., 2008), notably due to organic phosphorus increment. Experiments of long duration also found that the available P is higher in wastewater irrigated soils than in rainwater irrigated soils (Rusan et al., 2007).

The highest values of available P observed in the soil surface layer in T1, T2, and T4 (Table 5) corroborate the results obtained by Rusan et al. (2007) and Herpin et al. (2007) and can be attributed to several mechanisms, as the following: (i) increased P supply from wastewater, which contains this nutrient (Medeiros et al., 2007), (ii) mineralization of organic matter added by wastewater, which accumulates in the soil surface layer (Kiziloglu et al., 2008), (iii) P adsorption near the point of wastewater application, since this is a very immobile element, and (iv) possible P desorption or dissolution due to pH increase (Herpin et al., 2007). Liang et al. (2010) found that soil from rural areas of China with mineralogy similar to Fluvic Neosol (with high amount of kaolinite) showed high P content in wastewater due to the low adsorption capacity of the soil.

The organic matter content presented significant differences for treatment effect only in the surface layer. In general, it seems that there are lower levels of organic matter at depth, probably due to the short duration of the experiment. So, a longer wastewater application could favor the translocation of organic compounds to deeper layers, as verified by Rusan et al. (2007).

The levels of verified organic matter in the superficial layer, especially in wastewater treatments (T1, T2, and T4), corroborate the results obtained by Rusan et al. (2007), Herpin et al. (2007), and Sandri et al. (2009) in wastewater irrigation in soils cultivated with forage crops, pasture, and coffee, respectively. These results suggest very low leaching of carbon in wastewater irrigated soils, especially in short duration experiments (Herpin et al., 2007).

On the other hand, it is reported that wastewater irrigation in tropical soils does not change organic matter (Leal et al., 2010) or even decreases it (Duarte et al., 2008), which may be related to short duration period of the experiments or to a higher mineral N concentration, that increases microbial activity.

Organic matter is one of the most important soil quality indicators, especially with regard to nutrient cycling. Its presence is important for metal mobility control and to improve soil structure (Silva & Mendonça, 2007). Thus, the increment of its concentration in the soil surface layer is important and should be considered in wastewater reuse designs.

No significant effect of water source has been verified on the available Fe²⁺ and Zn²⁺ concentrations in the soil samples, but there were significant differences for Mn²⁺ and Cu²⁺ concentrations (Table 6). The results for Fe²⁺ and Zn²⁺ are in accordance with those obtained by Xu et al. (2010) in short duration (three years) wastewater irrigation, suggesting that these wastewater metal concentrations are not high enough to cause environmental impacts in experiments of such duration.

The Cu²⁺ concentration was significantly lower in T3 than in T1, T2, and T4 (treatment means). Castor bean absorbs this ion, with no restitution by wastewater, as occurred in T1 and T2 and as verified by Liu et al. (2005), during rice, wheat, corn, and vegetables grown. Figueroa et al. (2008) found that the castor bean plant is highly demanding to this micronutrient. The ranges of Cu²⁺ concentration are in agreement with those observed by Varallo et al. (2010), but are very low compared to the ranges verified by Sandri et al. (2009), even though the both researches were carried out with wastewater in Oxisols.

The lower mean concentration of Mn²⁺ was observed in T4 (treatment means), probably due to the formation of precipitates with carbonates and phosphates which were added by wastewater and released during the organic matter mineralization, making manganese unavailable, because these anions have a high affinity to chelate this metal cation (He et al., 2010). In T1, these mechanisms probably had a lower magnitude, due to castor bean absorption of such responsible ions (H₂PO₄^-, Mg²⁺, and Cu²⁺), minimizing the chelation, increasing the non-specific adsorption and the Mn²⁺ concentration.

In general terms, it was observed that all studied cationic micronutrients present a low soil mobility and tend to accumulate in the upper layers. According to some other studies (Rusan et al., 2007; Kiziloglu et al., 2008; Xu et al., 2010), the mobility of these elements to deeper layers in wastewater irrigated soils is not common, because it is closely related to the organic matter distribution in the soil profile.

CONCLUSIONS

1. Despite the short duration of the experiment, there were significant changes in soil chemical attributes due to the wastewater application.

2. The wastewater application in the castor bean crop increased phosphorous, calcium, potassium, and organic matter concentrations, mainly in the superficial layer of soil.

3. The disposal of wastewater on Fluvic Neosol not cultivated with castor bean increased the magnesium concentration in soil

4. The wastewater irrigation did not change pH, neither iron and zinc concentration in soil.

ACKNOWLEDGMENTS

This work was supported by CNPq (Process No. 552868/2007-8) and EMBRAPA (02.09.07.000.00.00). The authors would like to thanks João Paulo Saraiva Morais for English the grammar and spelling review.

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Publication Dates

• Publication in this collection
  07 May 2013
• Date of issue
  May 2013