Immediate Immobilization of Labeled Ammonium Sulfate and Urea Nitrogen in Soils

Okereke, G. U.; Meints, V. W.

doi:10.1097/00010694-198508000-00005

Cited by 27 publications

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“…12.6% of the added fertilizer N is immobilized at time 0 and another 10.6% is immobilized at day 4. This quick immobilization is also observed by Okereke and Meints (1985), who provided evidence that immobilization of some fertilizer N occurs within a matter of hours after application. The mineralization of the newly immobilized fraction obviously did not take place during the growing season.…”

Section: Discussionsupporting

confidence: 66%

The course of 15N-ammonium nitrate in a spring barley cropping system

et al. 1993

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15N-labelled ammonium nitrate was applied to spring barley growing on a Cambisol soil in western Switzerland. Immobilization, plant uptake and disappearance of inorganic nitrogen were followed at frequent intervals. Fertilizer nitrogen disappeared shortly after its application, mainly through immobilization by soil microorganisms and absorption by the crop. Some of the added nitrogen was probably denitrified as a result of humid conditions during the first days after fertilizer application. At the end of the growing season, 31% of the added nitrogen was recovered from the aerial barley plants, and 56% was immobilized by microorganisms. Most of the fertilizer nitrogen not used by the crop was immobilized in the upper 0-30 cm soil layer. This prevented downward movement of nitrate and limited nitrogen losses. Fertilizer efficiency was mainly determined by the competition between crop uptake and microbial immobilization. Careful consideration of the time of fertilization, taking into account plant growth and weather conditions, can result in an increase in fertilizer efficiency and minimal pollution.

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Section: Discussionsupporting

confidence: 66%

The course of 15N-ammonium nitrate in a spring barley cropping system

et al. 1993

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“…Assuming microorganisms use 15-30 parts of carbon for each part of nitrogen, low C/N ratios were often considered being responsible for higher emissions of ammonia (Okereke and Meints, 1985;Pagans et al, 2006;Tiquia and Tam, 2000;Zhu, 2007), whereas high C/N ratios would allow to immobilize and even fix nitrogen (Liang et al, 2006). However, as reported by Kirchmann and Witter (1989), many authors did not observe any reduction of ammonia emissions as C/N was increased.…”

Section: Introductionmentioning

confidence: 99%

Comparison of five organic wastes regarding their behaviour during composting: Part 2, nitrogen dynamic

et al. 2010

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Author-produced version of the article published in Waste Management Original publication available at www.elsevier. com -doi:10.1016/j.wasman.2009.10.018 2 Abstract 1 This paper aimed to compare household waste, separated pig solids, food waste, pig slaughterhouse sludge 2 and green algae regarding processes ruling nitrogen dynamic during composting. For each waste, three 3 composting simulations were performed in parallel in three similar reactors (300L), each one under a constant 4 aeration rate. The aeration flows applied were comprised between 100 and 1100 L/h. The initial waste and the 5 compost were characterized through the measurements of their contents in dry matter, total carbon, Kjeldahl and 6 total ammoniacal nitrogen, nitrite and nitrate. Kjeldahl and total ammoniacal nitrogen and nitrite and nitrate 7were measured in leachates and in condensates too. Ammonia and nitrous oxide emissions were monitored in 8 continue. The cumulated emissions in ammonia and in nitrous oxide were given for each waste and at each 9 aeration rate. The paper focused on process of ammonification and on transformations and transfer of total 10 ammoniacal nitrogen. The parameters of nitrous oxide emissions were not investigated. The removal rate of 11 total Kjeldahl nitrogen was shown being closely tied to the ammonification rate. Ammonification was modelled 12 thanks to the calculation of the ratio of biodegradable carbon to organic nitrogen content of the biodegradable 13 fraction. The wastes were shown to differ significantly regarding their ammonification ability. Nitrogen 14 balances were calculated by subtracting nitrogen losses from nitrogen removed from material. Defaults in 15 nitrogen balances were assumed to correspond to conversion of nitrate even nitrite into molecular nitrogen and 16 then to the previous conversion by nitrification of total ammoniacal nitrogen. The pool of total ammoniacal 17 nitrogen, i.e. total ammoniacal nitrogen initially contained in waste plus total ammoniacal nitrogen released by 18 ammonification, was calculated for each experiment. Then, this pool was used as the referring amount in the 19 calculation of the rates of accumulation, stripping and nitrification of total ammoniacal nitrogen. Separated pig 20 solids were characterised by a high ability to accumulate total ammoniacal nitrogen. Whatever the waste, the 21 striping rate depended mostly on the aeration rate and on the pool concentration in biofilm. The nitrification rate 22 was observed as all the higher as the concentration in total ammoniacal nitrogen in the initial waste was low. 23Thus, household waste and green algae exhibited the highest nitrification rates. This result could mean that in 24 case of low concentrations in total ammoniacal nitrogen, a nitrifying biomass was already developed and that 25 this biomass consumed it. In contrast, in case of high concentrations, this could traduce some difficulties for 26 nitrifying microorganisms to develop. 27

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“…Plant uptake of urinary nutrients is well described (Okereke and Meints, 1985;Nannipieri et al, 1990), whereas there is a shortage of information concerning the regulation of atmospheric losses from urine patches. Urine patches are well-known hot-spots of N 2 O emission (e.g., Yamulki et al, 1998;de Klein et al, 2001), but emission patterns are difficult to predict since there are several potential sources (Davidson, 1991;Killham, 1986;Venterea and Rolston, 2000) and complex interactions with soil environmental conditions (e.g., de Klein and van Logtestijn, 1994;Koops et al, 1997).…”

Section: Introductionmentioning

confidence: 99%

Short‐term N₂O, CO₂, NH₃ fluxes, and N/C transfers in a Danish grass‐clover pasture after simulated urine deposition in autumn

Bol¹,

Petersen²,

Christofides³

et al. 2004

Z. Pflanzenernähr. Bodenk.

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Urine patches are significant hot‐spots of C and N transformations. To investigate the effects of urine composition on C and N turnover and gaseous emissions from a Danish pasture soil, a field plot study was carried out in September 2001. Cattle urine was amended with two levels of 13C‐ and 15N‐labeled urea, corresponding to 5.58 and 9.54 g urea‐N l–1, to reflect two levels of protein intake. Urine was then added to a sandy‐loam pasture soil equivalent to a rate of 23.3 or 39.8 g urea‐N m–2. Pools and isotopic labeling of nitrous oxide (N2O) and CO2 emissions, extractable urea, ammonium (NH4+), and nitrate (NO3–), and plant uptake were monitored during a 14 d period, while ammonia (NH3) losses were estimated in separate plots amended with unlabeled urine. Ammonia volatilization was estimated to account for 14% and 12% of the urea‐N applied in the low (UL) and high (UH) urea treatment, respectively. The recovery of urea‐derived N as NH4+ increased during the first several days, but isotopic dilution was significant, possibly as a result of stress‐induced microbial metabolism. After a 2 d lag phase, nitrification proceeded at similar rates in UL and UH despite a significant difference in NH4+ availability. Nitrous oxide fluxes were low, but generally increased during the 14 d period, as did the proportion derived from urea‐N. On day 14, the contribution from urea was 23% (UL) and 13% (UH treatment), respectively. Cumulative total losses of N2O during the 14 d period corresponded to 0.021% (UL) and 0.015% (UH) of applied urea‐N. Nitrification was probably the source of N2O. Emission of urea‐derived C as CO2 was only detectable within the first 24 h. Urea‐derived C and N in above‐ground plant material was only significant at the first sampling, indicating that uptake of urine‐C and N via the leaves was small. Urine composition did not influence the potential for N2O emissions from urine patches under the experimental conditions, but the importance of site conditions and season should be investigated further.

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Immediate Immobilization of Labeled Ammonium Sulfate and Urea Nitrogen in Soils

Cited by 27 publications

References 0 publications

The course of 15N-ammonium nitrate in a spring barley cropping system

The course of 15N-ammonium nitrate in a spring barley cropping system

Comparison of five organic wastes regarding their behaviour during composting: Part 2, nitrogen dynamic

Short‐term N₂O, CO₂, NH₃ fluxes, and N/C transfers in a Danish grass‐clover pasture after simulated urine deposition in autumn

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Immediate Immobilization of Labeled Ammonium Sulfate and Urea Nitrogen in Soils

Cited by 27 publications

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The course of 15N-ammonium nitrate in a spring barley cropping system

The course of 15N-ammonium nitrate in a spring barley cropping system

Comparison of five organic wastes regarding their behaviour during composting: Part 2, nitrogen dynamic

Short‐term N2O, CO2, NH3 fluxes, and N/C transfers in a Danish grass‐clover pasture after simulated urine deposition in autumn

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Short‐term N₂O, CO₂, NH₃ fluxes, and N/C transfers in a Danish grass‐clover pasture after simulated urine deposition in autumn