Nitrate Reduction in the Subsoil

Lind, Anne-Margrethe

doi:10.1007/978-1-4757-9972-9_10

Cited by 16 publications

(10 citation statements)

References 5 publications

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“…6b). Small nitrate concentrations in groundwater can be explained by chemical denitrification associated with the oxidation of Fe++ to F e + + + (Lind & Pedersen, 1976;Rasmussen, 1980). The small increases in nitrate concentration of water samples taken from the 4 m depth at the start of each season suggest that leaching of agricultural nitrogen to the groundwater occurs within periods as short as one rainy season at this site.…”

Section: Groundwater Conditionsmentioning

confidence: 99%

Nitrate leaching in field lysimeters at an agricultural site in Zimbabwe

Kamukondiwa

Bergström

1994

Soil Use and Management

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Abstract. Nitrate leaching in lysimeters containing a tropical sandy agricultural soil was studied over two summers with maize (Zea mays L.) and one winter season with wheat (Triticum aestivum L.). The treatments included two moisture regimes and two nitrogen sources, cattle manure and inorganic fertilizer‐N (either ammonium nitrate or ammonium sulphate) applied at 100 kg N/ha in the summers. Neither manure nor fertilizer‐N was applied in the intervening winter. Leachate volume from the manured lysimeters was mostly larger than from fertilized ones because of poor growth and less evapotranspiration. The largest seasonal nitrate loads (17–39 kg N/ha) were obtained in the wet summer immediately after installation of the lysimeters. Nitrate loads in winter (3.7–18.6 kg N/ha) were larger than those obtained in fertilized (0.6 and 9.3 kg N/ha) and manured (0.3 and 3.0 kg N/ha) lysimeters for the two moisture regimes in the second summer. The drier conditions in the second summer decreased N‐mineralization and leaching of manure.

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Section: Groundwater Conditionsmentioning

confidence: 99%

Nitrate leaching in field lysimeters at an agricultural site in Zimbabwe

Kamukondiwa

Bergström

1994

Soil Use and Management

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“…Ling and El-Kadi (1998);Yamaguchi et al (1996);Starr et al (1974);Starr and Gillham (1993);Misra et al (1974);Ardakani et al (1974aArdakani et al ( , 1974b;Lind (1983);Slater and Capone (1987);Anderson (1998);Trudell et al (1986);Smith and Duff (1988);Bengtsson and Annadotter (1989);Francis et al (1989);Obenhuber and Lowrance (1991);Smith et al (1991);Ekpete and Cornfield (1965);Christensen et al (1989);Bradley et al (1992);Tesoriero et al (…”

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confidence: 99%

Model Parameters for Simulating Fate and Transport of On‐Site Wastewater Nutrients

et al. 2005

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This paper presents a critical review of model-input parameters for transport of on-site wastewater treatment system (OWS) pollutants. Approximately 25% of the U.S. population relies on soil-based OWS for effective treatment and protection of public health and environmental quality. Mathematical models are useful tools for understanding and predicting the transport and fate of wastewater pollutants and for addressing water-budget issues related to wastewater reclamation from site to watershed scales. However, input parameters for models that simulate fate and transport of OWS pollutants are not readily obtained. The purpose of this analysis is to illustrate an objective, statistically supported method for choosing model-input parameters related to nitrogen (N) and phosphorus (P). Data were gathered from existing studies reported in the literature. Cumulative frequency distributions (CFDs) are provided for OWS effluent concentrations of N and P, nitrification and denitrification rates, and linear sorption isotherm constants for P. When CFDs are not presented, ranges and median values are provided. Median values for model-input parameters are as follows: total N concentration (44 mg/L), nitrate-N (0.2 mg/L), ammonium (60 mg/L), phosphate-P (9 mg/L), organic N (14 mg/L), zero-order nitrification rate (264 mg/L/d), first-order nitrification (2.9/d), first-order dentrification (0.025/d), maximum soil capacity for P uptake (237 mg/kg), linear sorption isotherm constant for P (15.1 L/kg), and OWS effluent flow rates (260 L/person/d).

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“…The nitrite may for example react inorganically with Fe 2 + in the mud (see e.g. Lind, 1985;Chalamet and Bardin, 1977): 8 H+ + 2 NO£ + 6 Fe 2+ -6 Fe 3+ + N 2 + 4 H 2 0 while other reduced compounds (NO e.g.) may be formed as well.…”

Section: Discussionmentioning

confidence: 99%

The nitrogen cycle in shallow water sediment systems of rice fields. Part 1: The denitrification process

1988

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Denitrification causes important losses of N-fertilizer in rice-fields, where high temperature and high production of organic matter favour denitrification losses. Two techniques have been used to quantify the denitrification losses: the 15 N technique, which can be used to quantify the amount finally incorporated, and the acetylene inhibition technique which is a direct measure of the quantities lost.Both techniques were applied in enclosures (diameter = 44 cm) in the field while moreover bio-assays in 3 1 glass beakers were carried out. In all experiments where nitrate was added we found a rapid decrease of nitrate; usually about 30-50°o of the nitrate that disappeared was recovered as N 2 0. As in one experiment, in which we measured the N 2 0 disappearance rate as well, the N 2 0 itself decreased at a rather constant rate of 20% per day, a correction must be made for this N 2 0 decrease in the calculations of the nitrate disappearance rate. Although we have only one series in which the decrease of N 2 0 was measured, the mathematical analysis indicates that as much as 80°o of the N-fertilizer is actually lost. This figure is in full agreement with the 15 N experiments; if the 'SN was applied early only about 7% was recovered in soil and plants, while if it was applied later (after 7 weeks) about 20% was incorporated.Denitrification rate could be fitted on an negative exponential regression line; the rate constant increased during the summer. It is suggested that organic matter caused this increase.During denitrification considerable quantities of nitrite appear, which later on disappear again by processes still unknown; the nature of the available organic matter may be important for this nitrite production.With N-serve we tried to inhibit NH 3 oxidation. In this way we tried to prevent the considerable N losses and to demonstrate that the nitrite produced in our experiments was not derived from NH 3 oxidation. Nserve, however, had very little influence. It is probably inactivated by absorption onto the sediments.From these results it is suggested that the efficiency of N-application may be considerably increased by using low doses of N-fertilizer, but applied late in the growing season, e.g. 7 weeks after sowing. This favours environmental protection as well. IntroductionTheir energy input by primary production is brought about not only by the rice itself, but also by several Rice-fields are sediment -water ecosystems with a other plants (e.g. Chara) and phytoplankton. As inhigh primary production. They are therefore ideal dividuals of the latter two die constantly throughout systems to study processes occuring in sediments. the season, they provide a large reservoir of organic

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Nitrate Reduction in the Subsoil

Cited by 16 publications

References 5 publications

Nitrate leaching in field lysimeters at an agricultural site in Zimbabwe

Nitrate leaching in field lysimeters at an agricultural site in Zimbabwe

Model Parameters for Simulating Fate and Transport of On‐Site Wastewater Nutrients

The nitrogen cycle in shallow water sediment systems of rice fields. Part 1: The denitrification process

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