Growth and nitrogen fixation in soybean treated with doses of composted sewage sludge

The use of sewage sludge is a highly promising practice for the development of sustainable agricultural systems. The objective of this study was to evaluate doses of sewage sludge composted with and without Rhizobium inoculation in leaf N content, nodule number, nodule dry weight and plant during flowering. The experiment was conducted in the greenhouse of the Department of Soil Science and Natural Resources College of Agricultural Sciences of Botucatu, using as substrate used in vessels of 30 liters a Red Yelow Latosol sandy texture with experimental design adopted was randomized blocks constituted for 10 treatments and five doses of composted sewage sludge (0, 10, 20, 30, 40 t ha(-1)) with or without inoculation Bradyrhizobium japonic with three replications. There was an increase in the number and dry weight of nodules and shoot dry mass of soybeans due to the increase of the dose of sludge up to a dose of 20 t ha(-1) and after this dose there was a decrease of these parameters. At a dose of 10 t ha(-1) sludge compost inoculated seeds showed higher for foliar concentrations of N and number of nodules compared with uninoculated seeds. At a dose of 30 t ha(-1) inoculated seeds were higher compared to uninoculated in all parameters.

Biorremediação de solo contaminado por isobutanol, Bis-2-etil-hexilftalato e Di-isodecilftalato

Embora os ftalatos sejam um dos poluentes mais frequentemente encontrados no meio ambiente, há escassez de dados na literatura sobre biorremediação de solos tropicais contaminados por esses compostos. Por esse motivo, este estudo avaliou a biorremediação de um solo contaminado com os plastificantes DEHP (Bis-2-etilhexilftalato), DIDP (Di-isodecilftalato) e álcool isobutílico, por uma indústria no Estado de São Paulo. A biorremediação ocorreu pela utilização de microrganismos presentes no solo e pela adição de inóculo adaptado em reator em fase de lama. O reator foi monitorado durante 120 dias, sendo corrigida apenas a umidade do solo. Os resultados indicaram que a biodegradação dos ftalatos seguiu uma cinética de primeira ordem e a biorremediação ocorreu na faixa de pH entre 7,4 e 8,4 e temperaturas entre 17 e 25 ºC, com eficiência de remoção de contaminantes acima de 70 %. Após 120 dias, o teor de DEHP estava abaixo de 4 mg kg-1, limite estipulado pela legislação brasileira para solo de uso residencial.

CHARACTERIZATION AND CLASSIFICATION OF SOILS IN THE TAQUARI RIVER BASIN - PANTANAL REGION, STATE OF MATO GROSSO DO SUL, BRAZIL

Among the soils in the Mato Grosso do Sul, stand out in the Pantanal biome, the Spodosols. Despite being recorded in considerable extensions, few studies aiming to characterize and classify these soils were performed. The purpose of this study was to characterize and classify soils in three areas of two physiographic types in the Taquari river basin: bay and flooded fields. Two trenches were opened in the bay area (P1 and P2) and two in the flooded field (P3 and P4). The third area (saline) with high sodium levels was sampled for further studies. In the soils in both areas the sand fraction was predominant and the texture from sand to sandy loam, with the main constituent quartz. In the bay area, the soil organic carbon in the surface layer (P1) was (OC) > 80 g kg(-1), being diagnosed as Histic epipedon. In the other profiles the surface horizons had low OC levels which, associated with other properties, classified them as Ochric epipedons. In the soils of the bay area (P1 and P2), the pH ranged from 5.0 to 7.5, associated with dominance of Ca2+ and Mg2+, with base saturation above 50 % in some horizons. In the flooded fields (P3 and P4) the soil pH ranged from 4.9 to 5.9, H+ contents were high in the surface horizons (0.8-10.5 cmol(c) kg(-1)), Ca2+ and Mg-2 contents ranged from 0.4 to 0.8 cmol(c) kg(-1) and base saturation was < 50 %. In the soils of the bay area (P1 and P2) iron was accumulated (extracted by dithionite - Fed) and OC in the spodic horizon; in the P3 and P4 soils only Fed was accumulated (in the subsurface layers). According to the criteria adopted by the Brazilian System of Soil Classification (SiBCS) at the subgroup level, the soils were classified as: P1: Organic Hydromorphic Ferrohumiluvic Spodosol. P2: Typical Orthic Ferrohumiluvic Spodosol. P3: Typical Hydromorphic Ferroluvic Spodosol. P4: Arenic Orthic Ferroluvic Spodosol.

CHARACTERIZATION OF REGOSOLS IN THE SEMIARID REGION OF PERNAMBUCO, BRAZIL

CHARACTERIZATION OF REGOSOLS IN THE SEMIARID REGION OF PERNAMBUCO, BRAZIL Studies on soil characterization in unexplored regions, besides the generation of data banks for the soil classes of the country, also produce scientific information about soil properties, important for the development of good management practices and sustainable land use. One of the main soil classes in the semiarid region of Pernambuco State, the Regosols, cover about 27 % of the state area, and are used mainly for family agriculture. Due to different geological and climatic aspects Regosols with different chemical, physical and mineralogical properties are found in Pernambuco, which were characterized for the semiarid region of the State. Five Regosol profiles were selected in different regions of the State (P1=Sao Caetano; P2=Lagoa do Ouro; P3=Caetes; P4=Sao Joao; P5=Parnamirim). The soils were morphologically characterized and samples collected from all horizons and the bedrock. Routine physical and chemical analyses were carried out for soil classification of all samples and mineralogical analyses of the coarse fractions (gravel and sand) by optical microscopy and of the silt and clay fractions by X ray diffraction (XRD), as well as petrographic analyses of the rock samples. The results showed similarities between the soils, with a low degree of pedogenetic development, varying from medium to very deep, with the horizon sequence A-AC-C-Cr and a sandy to sandy loam texture. In the deeper layers of two profiles (P1 and P5), a solodic character was observed. Organic matter and available phosphorus content were low in all studied soils. Despite the low levels of exchangeable cations, all soil profiles showed high base saturation. The mineralogical composition of gravel, sand and silt fractions consisted, essentially, of quartz, followed by feldspars and mica, supporting the results of the petrographic analysis of the bedrock. Kaolinite was the main clay mineral in all studied profiles and horizons, indicating an important monosialitization process in autochthonous soils of a typical semiarid region. In soil profile P2, at a lower landscape position, smectite minerals were observed, with mixing phases of montmorillonite, beidelite or nontronite, indentified by the Greene-Kelly test in the DRX analysis.

Bioremediation of PAHs - Limitations and soultions

Introduction 1.1 Occurrence of polycyclic aromatic hydrocarbons (PAH) in the environment Worldwide industrial and agricultural developments have released a large number of natural and synthetic hazardous compounds into the environment due to careless waste disposal, illegal waste dumping and accidental spills. As a result, there are numerous sites in the world that require cleanup of soils and groundwater. Polycyclic aromatic hydrocarbons (PAHs) are one of the major groups of these contaminants (Da Silva et al., 2003). PAHs constitute a diverse class of organic compounds consisting of two or more aromatic rings with various structural configurations (Prabhu and Phale, 2003). Being a derivative of benzene, PAHs are thermodynamically stable. In addition, these chemicals tend to adhere to particle surfaces, such as soils, because of their low water solubility and strong hydrophobicity, and this results in greater persistence under natural conditions. This persistence coupled with their potential carcinogenicity makes PAHs problematic environmental contaminants (Cerniglia, 1992; Sutherland, 1992). PAHs are widely found in high concentrations at many industrial sites, particularly those associated with petroleum, gas production and wood preserving industries (Wilson and Jones, 1993). 1.2 Remediation technologies Conventional techniques used for the remediation of soil polluted with organic contaminants include excavation of the contaminated soil and disposal to a landfill or capping - containment - of the contaminated areas of a site. These methods have some drawbacks. The first method simply moves the contamination elsewhere and may create significant risks in the excavation, handling and transport of hazardous material. Additionally, it is very difficult and increasingly expensive to find new landfill sites for the final disposal of the material. The cap and containment method is only an interim solution since the contamination remains on site, requiring monitoring and maintenance of the isolation barriers long into the future, with all the associated costs and potential liability. A better approach than these traditional methods is to completely destroy the pollutants, if possible, or transform them into harmless substances. Some technologies that have been used are high-temperature incineration and various types of chemical decomposition (for example, base-catalyzed dechlorination, UV oxidation). However, these methods have significant disadvantages, principally their technological complexity, high cost , and the lack of public acceptance. Bioremediation, on the contrast, is a promising option for the complete removal and destruction of contaminants. 1.3 Bioremediation of PAH contaminated soil & groundwater Bioremediation is the use of living organisms, primarily microorganisms, to degrade or detoxify hazardous wastes into harmless substances such as carbon dioxide, water and cell biomass Most PAHs are biodegradable unter natural conditions (Da Silva et al., 2003; Meysami and Baheri, 2003) and bioremediation for cleanup of PAH wastes has been extensively studied at both laboratory and commercial levels- It has been implemented at a number of contaminated sites, including the cleanup of the Exxon Valdez oil spill in Prince William Sound, Alaska in 1989, the Mega Borg spill off the Texas coast in 1990 and the Burgan Oil Field, Kuwait in 1994 (Purwaningsih, 2002). Different strategies for PAH bioremediation, such as in situ , ex situ or on site bioremediation were developed in recent years. In situ bioremediation is a technique that is applied to soil and groundwater at the site without removing the contaminated soil or groundwater, based on the provision of optimum conditions for microbiological contaminant breakdown.. Ex situ bioremediation of PAHs, on the other hand, is a technique applied to soil and groundwater which has been removed from the site via excavation (soil) or pumping (water). Hazardous contaminants are converted in controlled bioreactors into harmless compounds in an efficient manner. 1.4 Bioavailability of PAH in the subsurface Frequently, PAH contamination in the environment is occurs as contaminants that are sorbed onto soilparticles rather than in phase (NAPL, non aqueous phase liquids). It is known that the biodegradation rate of most PAHs sorbed onto soil is far lower than rates measured in solution cultures of microorganisms with pure solid pollutants (Alexander and Scow, 1989; Hamaker, 1972). It is generally believed that only that fraction of PAHs dissolved in the solution can be metabolized by microorganisms in soil. The amount of contaminant that can be readily taken up and degraded by microorganisms is defined as bioavailability (Bosma et al., 1997; Maier, 2000). Two phenomena have been suggested to cause the low bioavailability of PAHs in soil (Danielsson, 2000). The first one is strong adsorption of the contaminants to the soil constituents which then leads to very slow release rates of contaminants to the aqueous phase. Sorption is often well correlated with soil organic matter content (Means, 1980) and significantly reduces biodegradation (Manilal and Alexander, 1991). The second phenomenon is slow mass transfer of pollutants, such as pore diffusion in the soil aggregates or diffusion in the organic matter in the soil. The complex set of these physical, chemical and biological processes is schematically illustrated in Figure 1. As shown in Figure 1, biodegradation processes are taking place in the soil solution while diffusion processes occur in the narrow pores in and between soil aggregates (Danielsson, 2000). Seemingly contradictory studies can be found in the literature that indicate the rate and final extent of metabolism may be either lower or higher for sorbed PAHs by soil than those for pure PAHs (Van Loosdrecht et al., 1990). These contrasting results demonstrate that the bioavailability of organic contaminants sorbed onto soil is far from being well understood. Besides bioavailability, there are several other factors influencing the rate and extent of biodegradation of PAHs in soil including microbial population characteristics, physical and chemical properties of PAHs and environmental factors (temperature, moisture, pH, degree of contamination). Figure 1: Schematic diagram showing possible rate-limiting processes during bioremediation of hydrophobic organic contaminants in a contaminated soil-water system (not to scale) (Danielsson, 2000). 1.5 Increasing the bioavailability of PAH in soil Attempts to improve the biodegradation of PAHs in soil by increasing their bioavailability include the use of surfactants , solvents or solubility enhancers.. However, introduction of synthetic surfactant may result in the addition of one more pollutant. (Wang and Brusseau, 1993).A study conducted by Mulder et al. showed that the introduction of hydropropyl-ß-cyclodextrin (HPCD), a well-known PAH solubility enhancer, significantly increased the solubilization of PAHs although it did not improve the biodegradation rate of PAHs (Mulder et al., 1998), indicating that further research is required in order to develop a feasible and efficient remediation method. Enhancing the extent of PAHs mass transfer from the soil phase to the liquid might prove an efficient and environmentally low-risk alternative way of addressing the problem of slow PAH biodegradation in soil.

Methoden zur Analyse, Interpretation und Modellierung des elektrischen Widerstandes von archäologischen Steinstrukturen

In der Archäologie werden elektrische Widerstandsmessungen routinemäßig zur Prospektion von Fundstellen eingesetzt. Die Methode ist kostengünstig, leicht anwendbar und liefert in den meisten Fällen zuverlässige und leicht zu interpretierende Ergebnisse. Dennoch kann die Methode die archäologischen Strukturen in manchen Fällen nur teilweise oder gar nicht abbilden, wenn die bodenphysikalischen und bodenchemischen Eigenschaften des Bodens und der archäologischen Strukturen dies nicht zulassen. Der spezifische elektrische Widerstand wird durch Parameter wie Wassergehalt, Bodenstruktur, Bodenskelett, Bodentextur, Salinität und Bodentemperatur beeinflusst. Manche dieser Parameter, wie z.B. der Wassergehalt und die Bodentemperatur, unterliegen einer saisonalen Veränderung. Die vorliegende Arbeit untersucht den spezifischen elektrischen Widerstand von archäologischen Steinstrukturen und evaluiert die Möglichkeit, auf Grundlage von Geländemessungen und Laboranalysen archäologische Strukturen und Böden als numerische Modelle darzustellen. Dazu wurde eine Kombination von verschiedenen bodenkundlichen, geoarchäologischen und geophysikalischen Methoden verwendet. Um archäologische Strukturen und Bodenprofile als numerische Widerstandsmodelle darstellen zu können, werden Informationen zur Geometrie der Strukturen und ihren elektrischen Widerstandswerten benötigt. Dabei ist die Qualität der Hintergrundinformationen entscheidend für die Genauigkeit des Widerstandsmodells. Die Geometrie der Widerstandsmodelle basiert auf den Ergebnissen von Rammkernsondierungen und archäologische Ausgrabungen. Die an der Ausbildung des elektrischen Widerstands beteiligten Parameter wurden durch die Analyse von Bodenproben gemessen und ermöglichen durch Pedotransfer-Funktion, wie die Rhoades-Formel, die Abschätzung des spezifischen elektrischen Widerstandes des Feinbodens. Um den Einfluss des Bodenskeletts auf den spezifischen elektrischen Widerstand von Bodenprofilen und archäologischen Strukturen zu berechnen, kamen die Perkolationstheorie und die Effective Medium Theory zum Einsatz. Die Genauigkeit und eventuelle Limitierungen der Methoden wurden im Labor durch experimentelle Widerstandsmessungen an ungestörten Bodenproben und synthetischen Materialien überprüft. Die saisonale Veränderung des Wassergehalts im Boden wurde durch numerische Modelle mit der Software HYDRUS simuliert. Die hydraulischen Modelle wurden auf Grundlage der ermittelten bodenkundlichen und archäologischen Stratigraphie erstellt und verwenden die Daten von lokalen Wetterstationen als Eingangsparameter. Durch die Kombination der HYDRUS-Ergebnisse mit den Pedotransfer-Funktionen konnte der Einfluss dieser saisonalen Veränderung auf die Prospektionsergebnisse von elektrischen Widerstandsmethoden berechnet werden. Die Ergebnisse der Modellierungsprozesse wurden mit den Geländemessungen verglichen. Die beste Übereinstimmung zwischen Modellergebnissen und den Prospektionsergebnissen konnte für die Fallstudie bei Katzenbach festgestellt werden. Bei dieser wurden die Modelle auf Grundlage von archäologischen Grabungsergebnissen und detaillierten bodenkundlichen Analysen erstellt. Weitere Fallstudien zeigen, dass elektrische Widerstandsmodelle eingesetzt werden können, um den Einfluss von ungünstigen Prospektionsbedingungen auf die Ergebnisse der elektrischen Widerstandsmessungen abzuschätzen. Diese Informationen unterstützen die Planung und Anwendung der Methoden im Gelände und ermöglichen eine effektivere Interpretation der Prospektionsergebnisse. Die präsentierten Modellierungsansätze benötigen eine weitere Verifizierung durch den Vergleich der Modellierungsergebnisse mit detailliertem geophysikalischem Gelände-Monitoring von archäologischen Fundstellen. Zusätzlich könnten elektrische Widerstandsmessungen an künstlichen Mauerstrukturen unter kontrollierten Bedingungen zur Überprüfung der Modellierungsprozesse genutzt werden.