Mineralogy and phosphorus adsorption in soils of south and central-west Brazil under conventional and no-tillage systems

Mineralogia e adsorção de fósforo em solos sob preparo convencional e plantio direto nas regiões sul e centro-oeste do Brasil

SOLOS / SOILS

Mineralogy and phosphorus adsorption in soils of south and central-west Brazil under conventional and no-tillage systems

Mineralogia e adsorção de fósforo em solos sob preparo convencional e plantio direto nas regiões sul e centro-oeste do Brasil

Jessé Rodrigo Fink^I; Alberto Vasconcellos Inda^I*; Cimélio Bayer^I; José Torrent^II; Vidal Barrón^II

^IDepartamento de Solos, Universidade Federal do Rio Grande do Sul, Av. Bento Gonçalves, 7712, Cx. Postal 15100, 97105-400, Porto Alegre, Rio Grande do Sul, Brazil, *Author for correspondence. E-mail: [e-mail]

^IIDepartamento de Agronomía, Universidad de Córdoba, Córdoba, Spain

ABSTRACT

The low phosphorus availability in tropical and subtropical soils, normally related to adsorption of phosphate to the minerals surfaces, can be attenuated when organic matter (OM) accumulates in the soils. Herein, we report the results of long-term experiments (18–32 years) aimed at quantifying the maximum phosphorus adsorption capacity (MPAC) and its determinant mineralogical variables in Brazilian soils and at assessing the effect of no-tillage (NT) in mitigating the phosphorus adsorption of soils. The MPAC of soils ranged from 297 to 4,561 mg kg^-1 in the 0.00–0.10 m layer and from 285 to 4,961 mg kg-1 in the 0.10–0.20 m layer. The MPAC was correlated with the concentrations of iron oxides, goethite and ferrihydrite, gibbsite/(gibbsite+kaolinite) ratio and the specific surface area. The OM increased in the 0.00–0.10 m layer of NT soils, which was not reflected on the decrease of MPAC for the no-tillage soils.

Keywords: iron oxides, gibbsite, organic carbon, phosphate.

RESUMO

A baixa disponibilidade de fósforo em solos tropicais e subtropicais, normalmente relacionada à adsorção de fosfato pelas superfícies minerais, pode ser atenuada quando matéria orgânica (MO) é acumulada nos solos. Em experimentos de longa duração (18-32 anos) em solos brasileiros, o estudo objetivou quantificar a capacidade máxima de adsorção de fósforo (CMAP) e as variáveis mineralógicas determinantes, bem como verificar o efeito do plantio direto em mitigar a adsorção de fósforo nos solos. A CMAP dos solos variou de 297 a 4.561 mg kg^-1 na camada 0,00–0,10 m e de 285 a 4.961 mg kg^-1 na camada 0,10–0,20 m. A CMAP apresentou relação com a concentração de óxidos de ferro, de goethita e de ferrihydrita, com a razão gibbsita/(gibbsita+caulinita) e com a área superficial específica do solo. O conteúdo de MO aumentou na camada 0,00–0,10 m dos solos em plantio direto e não afetou a CMAP em comparação aos solos em sistema de preparo convencional.

Palavras-chave: óxidos de ferro, gibbsita, carbono orgânico, fosfato.

Introduction

Phosphorus is an essential plant nutrient that is usually present in forms of low availability in the highly weathered soils of tropical and subtropical regions from Brazil, a phenomenon that has been suggested as one of the main limiting factors for agricultural production (NOVAIS; SMYTH, 1999). This lack of available phosphorus mainly is attributed to its strong adsorption (this term is used for all forms of retention of the element) by mineral surfaces, making a part of the total phosphorus unavailable to plants (ALMEIDA et al., 2003; CESSA et al., 2009; JOHNSON; LOEPPERT, 2006).

The main minerals related to the adsorption of P in soils are iron (Fe) and aluminum (Al) oxides, which together with kaolinite, make up the dominant mineralogy in the clay fraction of most soils in the southern (subtropical) and central-western (tropical) regions of Brazil (NITZSCHE et al., 2008; SCHAEFER et al., 2008). Hematite and goethite are the predominant pedogenic Fe oxides, followed by maghemite and ferrihydrite, and gibbsite is Al oxide. The concentrations of these minerals in the soil and characteristics such as crystallinity and specific surface area vary with the parent material, intensity of weathering, composition of the soil solution and drainage conditions (MOTTA; KÄMPF, 1992; SCHAEFER et al., 2008) and may also be affected by soil management systems (SILVA NETO et al., 2008).

The degree of interaction between P and soil mineral constituents can be evaluated by the maximum phosphorus adsorption capacity (MPAC), which can be calculated by fitting the Langmuir equation, among others (OLSEN; WATANABE, 1957). Several studies have shown significant variations in the MPAC in well-drained soils with advanced weathering that are generally correlated with the crystalline phases of Fe and Al oxides (ALMEIDA et al., 2003; BARBIERI et al., 2009; BROGGI et al., 2010; CESSA et al., 2009; CURI; FRANZMEIER, 1984; FONTES; WEED, 1996; LAIR et al., 2009). Most authors have stressed that soils rich in goethite and gibbsite adsorb more P than those rich in hematite and kaolinite. Torrent et al. (1994), however, reported that the average P adsorption capacity per unit area is similar between goethite and hematite in soils and that the increased P adsorption in goethites is determined by structural features such as a larger specific surface area (SSA). Thus, the high SSA of poorly crystalline Fe oxides such as ferrihydrite, even in small concentrations in well-drained soils, may play a crucial role in P adsorption (JOHNSON; LOEPPERT, 2006; RANNO et al., 2007).

In addition to the mineralogical composition of the soil, attention has been focused on the role of organic matter (OM) in reducing P adsorption capacity and improving the availability of P for plants grown in a soil under a long-term conservation management system such as the no-tillage system (PAVINATO et al., 2009). Organic ligands in the soil solution compete with P for adsorption sites on the surface of minerals, thus are decreasing P adsorption by these minerals (LIU et al., 1999; MIKUTTA et al., 2006; SCHWERTMANN et al., 1986). However, there is no consensus on this issue, and some studies have failed to verify the ability of increased levels of organic C to reduce P adsorption (RANNO et al., 2007; RHEINHEIMER et al., 2003).

The objective of this study was to determine the MPAC in five highly weathered soils and to establish relationships with (i) the pedogenic Fe oxides content, (ii) the concentrations of specific phases of Fe oxides (goethite, hematite, maghemite and ferrihydrite), (iii) the proportions of gibbsite and kaolinite and (iv) the specific surface area of these soils. The ability of no-tillage system to reduce soil phosphorus adsorption in comparison with conventional tillage was also evaluated.

Material and methods

Description of sites and soil sampling

The study was based on five soils from different regions of Brazil (Table 1). Long-term experiments were conducted in these soils with successions and/or rotations of crops under conventional tillage (CT) and no-tillage (NT) systems. The experiments were set up in a randomized block design with three replicates. In each experimental replicate of both tillage systems (CT and NT), the soil was sampled as follows: (i) at depths of 0.00 to 0.10 m and 0.10 to 0.20 m, for a total 60 soil samples, and (ii) in the 0.00–0.20 m layer, for a total of 30 soil samples. Soil samples representing native grassland conditions were collected in areas adjacent to the experimental field at depths of 0.00 to 0.20 m for particle size analysis and the determination of the mineralogical composition of the soil by X-ray diffraction. After air-dried and ground, soil samples were passed through a 2-mm sieve to obtain the air-dried fine soil (ADFS) fractions.

Physical analyses

Particle size analysis was performed using the pipette method after dispersion of the particles by ultrasound. For this purpose, 20 g ADFS samples from the 0.00–0.20 m layer of each soil were added into 100 mL centrifuge tubes containing 80 mL of distilled water, which were subjected to various levels of energy according to the soil (between 200 and 2,100 J mL^-1) in a Vibracel ultrasound machine equipped with a 136 mm long × 13 mm diameter probe. To each soil, the energy required for the complete dispersion of soil primary particles was estimated from a previously determined calibration curve (NORTH, 1976). Having determined the soil particle size, the total clay fraction (Ø < 0.002 mm) of each soil sample was collected by sedimentation according to Stokes's Law. The suspended clay was flocculated with 0.1 M HCl, washed with an ethanol/water solution (1:1) and dried at 50°C.

The specific surface area (SSA) of the ADFS samples of the 0.00–0.10 m and 0.10–0.20 m layers were estimated using the water adsorption method at 20% relative humidity (QUIRK, 1955).

X-ray diffraction analysis

The mineralogical composition of the total clay and iron oxide concentrate fractions at a depth of 0.00-0.20 m of the soils under native grassland was determined by X-ray diffraction (XRD) (Siemens D5000 diffractometer with CoKα radiation and a Fe filter). Analyses were conducted on non-oriented slides for the total clay fraction (at a 2θ range of 4−52°) and the iron oxide concentrate fraction (at a 2θ range 20−70°). Iron oxides were concentrated by treating the total clay fraction with hot 5 mol L^-1 NaOH (KÄMPF; SCHWERTMANN, 1982). The minerals were identified based on the diffraction constant data provided by Brown and Brindley (1980).

Chemical analyses

The concentrations of extractable Ca⁺², Mg⁺², K⁺, Al⁺³, H+Al, pH and P were determined in the ADFS samples for the 0.00–0.20 m layer according to methods described by Embrapa (1997) and served as the basis for calculating the sum of bases (S), cation exchange capacity (CEC_pH7), base saturation (V) and aluminum saturation (m). The total organic carbon (organic C) contents in the ADFS samples of the 0.00–0.10 m and 0.10–0.20 m layers were determined by dry combustion in a carbon analyzer (Shimadzu VCSH).

Selective dissolutions of Fe oxides were prepared in the ADFS samples of the 0.00–0.10 m and 0.10–0.20 m layers. The Fe in pedogenic Fe oxides (Fe_d) was extracted with dithionite-citrate-bicarbonate at 80°C (MEHRA; JACKSON, 1960). The Fe in Fe oxides of low crystallinity (basically ferrihydrite, Fe_o) was extracted using 0.2 mol L^-1 ammonium oxalate at pH 3.0 in darkness (SCHWERTMANN, 1964). The levels of dissolved Fe were determined by atomic absorption spectroscopy (AAS).

The proportions of the different Fe oxides phases identified in the XRD analyses of the concentrated Fe oxides fraction were estimated from the areas of the 110 reflection plane of goethite (Gt-110), the 012 plane of hematite (Hm-012) and the 220 plane of maghemite (Mh-220) that were obtained using the Siemens DIFFRAC plus-EVA computer program. The Gt-110 reflection area was multiplied by 0.30 because the intensities of the Hm-012 and MH-220 reflections are 30% of the Gt-110 reflection intensity (ALMEIDA et al., 2003). The Al³⁺ substitution was estimated according to the regression Al(mol mol^-1)=17.30-5.72c (Å) in goethite (SCHULZE, 1984), according to the regression Al(mol mol^-1)=31.09-6.17a₀ (Å) in hematite (SCHWERTMANN et al., 1979) and according to the regression Al(mol mol^-1)=37.54-4.50a₀ (Å) in the maghemite (SCHWERTMANN; FECHTER, 1984). The concentration of each Fe oxide specific phase was obtained by allocation of the Fe content relative to the crystalline Fe oxides (Fe_d – Fe_o) according to their concentration in each soil and considering their chemical formulas. The gibbsite/(gibbsite + kaolinite) ratio, Gb/(Gb + Kt), was calculated from the diffraction patterns of non-oriented slides prepared from the clay total fraction according to the relationship between the intensity of the 002 reflection plane of gibbsite (I_Gb-002) and the 001 plane of kaolinite (I_Kt-001) (MOTTA; KÄMPF, 1992).

For the evaluation of P adsorption, 3.00-g ADFS samples were used, in duplicate, and each sample was equilibrated with 30 mL of KCl (0.02 mol L^-1) containing doses of 30, 60, 120, 240, 480, 960 or 1,920 mg L^-1 P for the Oxisols and 15, 30, 60, 120, 240, 480 or 960 mg L^-1 P for the Alfisol and Ultisol. The suspension was shaken horizontally for 5h (Oxisols) or 2h (Alfisol and Ultisol) [these times were based on the observed time course of adsorption (data not shown)], and then left to rest for 20h before measuring the P content in the supernatant according to the method of Murphy and Riley (1962). The amount of P adsorbed by the sample was estimated using the difference between the added P and the amount in the supernatant. The maximum phosphorus adsorption capacity (MPAC) was obtained from the parameters of the fitted Langmuir equation

where:

P_adsorbed is the P adsorbed in the sample, P_solution is the concentration in the solution, K is a constant related to the sorption energy, and P_max is the maximum P adsorption capacity.

Data analysis

The data analysis was performed with the Statistical Analysis System software (SAS for Windows). The Kolmogorov-Smirnov test for normality showed that at the 5% level the parameters follow a normal distribution only within the soil classes. In this case, comparison of means were performed with Tukey test (α = 0.05). Spearman nonparametric correlations (r_s) were obtained for parameters that were not normal distributed.

Results and discussion

Soil characteristics

The Alfisol and Ultisol developed from sandstone and granite, respectively, showed lower clay contents (≤ 228 g kg^-1 of soil) than the Oxisols developed from basalt (clay ≥ 596 g kg^-1 of soil) (Table 2).

The soil pH ranged from 4.8 to 5.2, with the exception of the Typic Hapludox, which exhibited pH values near 6.0. The pH reflected the levels of H+Al and Al saturation (m), and the Typic Hapludox had the lowest values for these parameters. The sum of bases (S) ranged from 2.96 to 9.79 cmol_c kg^-1 in the Ultic Hapludalf and Rhodic Hapludox soils, respectively, and Ca⁺² was the predominant cation. The CTC_pH7 values ranged from 7.3 cmol_c kg^-1 in the CT of Ultic Hapludalf to 16.6 cmol_c kg^-1 in the NT of Rhodic Hapludox, with base saturations (V) greater than 50% only in the Typic and Rhodic Hapludox soils. The levels of available P were higher in the NT than in the CT samples in three of the five soils, ranging from 9.5 mg kg-1 in the CT of Humic Hapludox to 59 mg kg-1 in the NT of Typic Hapludox.

The organic C content differed significantly among the soils (Figure 1) as the likely result of differences in clay content (Alfisol and Ultisol < Oxisols), mineralogy and pedoclimate that are known to affect the accumulation and stabilization of OM (Table 1). The significant effect of NT on the increase of organic C relative to CT was observed only in the 0.00–0.10 m layer in the Rhodic Paleudult and Humic Hapludox. With the exception of the Typic Hapludox, the organic C content decreased with increasing depth in all soils subjected to NT; however, this effect was not observed under CT (Figure 1).

The SSA values in the soils ranged from 9.9 to 63.4 m² g^-1 in both the NT and CT samples (Table 3). The SSA tended to be greater in the NT- than in the CT-treated soils, probably because of the increase in organic C in the no-tilled surface soil layer. The positive relationship (p < 0.0001) between SSA, estimated by the water-adsorption method, and organic C content was in sharp contrast with the inverse relationships observed in several studies in which the SSA was estimated by N₂ adsorption (AFIF et al., 1995; ALMEIDA et al., 2003). This discrepancy can be attributed to a more effective hindrance of N₂ to enter pores or covering the mineral surface by associated with clay fraction than the polar water molecule, thus difficulting the access and covering of the mineral surfaces (ALMEIDA et al., 2003).

Mineralogical composition and phosphorus adsorption capacity of the soils

The X-ray diffraction patterns in the total clay fraction (Figure 2a) revealed the predominance of kaolinite in the Rhodic Hapludox, Rhodic Paleudult and Ultic Hapludalf (Gb/(Gb+Kt) ≤ 0.10) (Table 3) associated with 2:1 or 2:1:1 minerals (Rhodic Hapludox and Ultic Hapludalf) and quartz (Rhodic Paleudult and Ultic Hapludalf) that occurred to a less extent. The Typic and Humic Hapludox soils showed predominance of gibbsite [Gb/(Gb+Kt) ≥ 0.69] with the presence of 2:1 or 2:1:1 minerals in the Humic Hapludox. In all soils, the goethite and hematite Fe oxides were present in the fraction of concentrated Fe oxides (Figure 2b). In the Ultic Hapludalf, Humic and Typic Hapludox soils, Gt/(Gt+Hm) ≥ 0.77, i.e. goethite predominated over hematite (Table 3). The Rhodic Hapludox showed a predominance of hematite over goethite [Gt/(Gt+Hm) = 0.05], whereas the proportions of goethite and hematite were similar in the Rhodic Paleudult (Table 3). The presence of maghemite was detected only in the Rhodic Hapludox (Figure 2b), where it occurs in significant proportion according to the ratio Mh/(Mh+Gt+Hm) = 0.36.

The Fe present in pedogenic Fe oxides (Fe_d) and the concentrations of the various Fe oxides identified in each soil are presented in Table 3. The Fe-for-Al substitution in the goethite, hematite and maghemite, as well as the chemical formulas considered in the allocation of Fe levels are listed in Table 4. In each soil, the Fe_d levels and the concentrations of Fe oxide phases were similar between the management systems and at both depths studied, whereas wide ranges were observed among the soils (Table 3). The highest Fe_d concentrations were observed in the Rhodic and Humic Hapludox developed from basalt (105–120 g kg^-1), whereas the Ultic Hapludalf and Rhodic Paleudult, formed from sandstone and granite, respectively, exhibited lower Fe_d values (7–15 g kg^-1). The ferrihydrite concentrations in the soil, estimated from the Fe extracted by ammonium oxalate (Fe_o), also showed a relationship with the parent material, ranging from 3.5 to 6.5 g kg^-1 in the Oxisols and from 1.1 to 2.2 g kg-1 in the Alfisoil and Ultisoil. A Fe_o/Fe_d < 0.11 in the soils indicated a predominance of crystalline phases of Fe oxides (SCHWERTMANN et al., 1982). Concentrations of crystalline Fe oxides showed significant amplitudes, where the contents of goethite ranged from 4.8 g kg-1 in Rhodic Paleudult to 121.2 g kg-1 in Humic Hapludox; hematite ranged from 4.0 g kg-1 in the Ultic Hapludalf to 100.5 g kg-1 in the Rhodic Hapludox. In the Rhodic Hapludox, where maghemite was detected, its concentration was approximately 61 g kg^-1 (Table 3).

MPAC varied greatly among the soils, but could be devided into three groups (Figure 3). In increasing order of MPAC, the Ultic Hapludalf and Rhodic Paleudult presented the lowest values (~300 mg kg^-1), followed by the Typic and Rhodic Hapludox (~1,100 mg kg^-1) and the Humic Hapludox, which showed the greatest P adsorption capacity (~4,700 mg kg^-1). As for the soil mineralogical attributes, the MPAC was positively correlated with Fe_d and Gb/(Gb+Kt (Table 5). The observed lower capacity of kaolinite to adsorb P compared with that of gibbsite (BARBIERI et al., 2009; BROGGI et al., 2010; CESSA et al., 2009; FONTES; WEED, 1996) has been related to the lower concentrations of OH sites on its surface (CELI et al., 2003).

Considering the different Fe oxides, MPAC was positively correlated with the concentration of goethite and ferrihydrite (Table 5). These results reinforce the importance of low crystallinity phases such as ferrihydrite in the adsorption of P (JOHNSON; LOEPPERT, 2006; RANNO et al., 2007), even at low concentrations in the soil, and the greater P adsorption capacity of goethite compared with hematite observed in previous studies (ALMEIDA et al., 2003; CESSA et al., 2009; CURI; FRANZMEIER, 1984; FONTES; WEED, 1996). In addition, the results suggest that the higher amount of P adsorption by goethite is related to its greater specific surface area, as evidenced by the significant relationship (p 0.0027) obtained between the concentration of goethite and the SSA values of the soils (Table 5), thus corroborating the results of Torrent et al. (1990, 1992, 1994). It should be noted that the formation of goethite is favored in environments that promote the accumulation of OM in the soil (BIGHAM et al., 2002), which suggests that the correlation between MPAC and organic C (Table 5) is affected by the covariance between the concentrations of goethite and organic C (p < 0.0001).

Regarding the relationships between the MPAC and the influential soil parameters, the lower MPACs of the Ultic Hapludalf and Rhodic Hapludox resulted from the kaolinitic mineralogy (Gb/(Gb+Kt) ≤ 0.10) combined with the low concentrations of iron oxides (Fe_d < 15 g kg^-1) and the consequently reduced SSA in these soils (SSA < 20 m² g^-1). The Typic and Rhodic Hapludox showed intermediate MPAC values compared with the other soils, but these soils were characterized by distinct combinations of mineralogical attributes. The greater concentration of pedogenic Fe oxides (115 < Fe_d < 120 g kg^-1) in the Rhodic Hapludox, due to the predominance of hematite and maghemite minerals, was compensated for in the Typic Hapludox by the concentration of goethite and the greater proportion of gibbsite [Gb/(Gb+Kt) = 0.69]. The high MPAC of the Humic Hapludox resulted from its gibbsitic mineralogy [Gb/(Gb+Kt) = 0.78] combined with a high concentration of Fe oxides (Fe_d > 100 g kg^-1), mainly due to the presence of goethite minerals, which resulted in the largest SSA of all the soils (60 < SSA <65 m² g^-1).

Effect of soil management systems on soil phosphorus adsorption capacity

The MPACs of all the soils were similar at the depths 0.0–00.10 m and 0.10–0.20 m (Figure 3), even with the greater concentration of organic C in the 0.00–0.10 m layers of the no-tilled Rhodic Paleudult and Humic Hapludox (Figure 1). An effect of the different soil management systems on MPAC was also not observed in two Oxisols and one Alfisol in southern Brazil in the study of Rheinheimer et al. (2003). These results contradict other studies indicating that the interactions between mineral surfaces and organic compounds reduce the P adsorption capacity of a soil (ALMEIDA et al., 2003; SCHWERTMANN et al., 1986), although these authors did not specifically evaluate the effect of management systems on MPAC; instead, they determined the MPAC of different soil classes.

The results of the present study may have been influenced by the depth of the surface layer assessed (0.00–0.10 m), thus supporting the explanation provided by Pavinato et al. (2010), who observed a change in the characteristics of P adsorption in the zone near the surface. The accumulation of organic C in the NT soil, which is normally highest in the first centimeters from the soil surface (0.00–0.025 m and 0.025–0.05 m), may have been diluted by sampling the 0.00–0.10 m layer. Additionally, the soil grinding procedure to obtain the ADFS destroys the aggregates formed under NT, thereby exposing the P adsorption sites that would be less exposed under the natural conditions of the management system.

Conclusion

The diversity of the mineralogical composition of the soils resulted in significant differences in the maximum phosphorus adsorption capacities among the soils. The P adsorption capacities of soils followed the sequence: Ultic Hapludalf ≈ Rhodic Paleudult < Typic Hapludox ≈ Rhodic Hapludox < Humic Haplodox, and the increase was positively related to the Fe in pedogenic Fe oxides, the concentrations of goethite and ferrihydrite and the gibbsite to kaolinite ratio, which were instrumental in increasing the specific surface area of soils. The maximum phosphorus adsorption capacity of each soil was not affected by long-term no-tillage system.

Acknowledgements

The authors thank CNPq for providing fellowships to A.V. Inda and C. Bayer, and financial support under Universal Edital (process 470718/2009-9; 481694/2011-0). This work was also partly financed by the Spain's Ministry of Science and Innovation (Project CGL 2010-15067) and the European Regional Development Fund.

Received on July 17, 2012.

Accepted on October 9, 2012.

License information: This is an open-access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.

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Publication Dates

• Publication in this collection
  08 Aug 2014
• Date of issue
  Sept 2014

History

• Accepted
  09 Oct 2012
• Received
  17 July 2012