Use of a urease inhibitor to mitigate ammonia emissions from urine patches.

Urine deposition by grazing livestock is the single largest source of ammonia (NH3) volatilisation losses in New Zealand. Urease inhibitors (UI) have been used to mitigate NH3 losses from fertiliser urea and animal urine. In previous trials, the UI effect in reducing NH3 emissions from urine has been measured by applying urine mixed with the UI to the pasture soil thus increasing the chances of better interaction of the UI in inhibiting the urease enzyme. However, these trials do not represent a realistic grazing scenario where only urine is deposited onto the soil. This current research aimed to identify the best time to spray nBTPT (a UI containing 0.025% N-(n-butyl) thiophosphoric triamide) onto pasture soil to reduce NH3 losses from urine patches. The treatments were: a control (without urine and nBTPT), urine alone at 530 kg N ha-1 and urine plus nBTPT. The UI was applied to the chambers and soil plots 5 and 3 days prior to urine deposition, on the same day and 1, 3 and 5 after urine deposition in autumn. Ammonia losses were measured using the dynamic chamber method. The application of the inhibitor prior to urine deposition reduced NH3 losses with reductions of 27.6% and 17.5% achieved for UAgr-5 and UAgr-3, respectively. However, reductions in NH3 emission were 0.6-2.9% for inhibitor applied post urine deposition. There was also a reduction in both soil NH4 +-N concentration and soil pH in comparison with urine alone or with the treatments where nBTPT was applied after urine deposition.

Nitrous oxide emissions from in situ deposition of N-labeled ryegrass litter in a pasture soil.

During pasture grazing, freshly harvested herbage (litterfall) is dropped onto soils from the mouths of dairy cattle, potentially inducing nitrous oxide (NO) emissions. Although the Intergovernmental Panel on Climate Change (IPCC) recommends accounting for NO emissions from arable crop residues in national inventories, emissions from the litterfall of grazed pasture systems are not recognized. The objective of this study was to investigate the potential of litterfall to contribute to NO emissions in a field study located on a pasture site in Canterbury, New Zealand (43°38.50' S, 172°27.17' E). We applied N-labeled perennial ryegrass ( L.) to the surface of a pastoral soil (Temuka clay loam) and, for up to 139 d thereafter, quantified the contribution of herbage decomposition to NO production and soil N dynamics. Litterfall contributed to the N enrichment of soil NO-N and NO-N pools. After 49 d, N recovery as NO equated to 0.93% of the surface-applied litter N, with 38 to 75% of the cumulative NO flux occurring within 4 to 10 d of treatment application. Emissions of NO likely resulted from ammonification followed by a coupling of nitrification and denitrification during litter decomposition on the soil surface. The emission factor of the litter deposited in situ was 1.2 ± 0.2%, which is not substantially greater than the IPCC default emission factor value of 1% for crop residues. Further in situ studies using different pasture species and litterfall rates are required to understand the microbial processes responsible for litter-induced NO emissions.

Intensive cattle grazing affects pasture litter-fall: an unrecognized nitrous oxide source.

The rationale for this study came from observing grazing dairy cattle dropping freshly harvested plant material onto the soil surface, hereafter called litter-fall. The Intergovernmental Panel on Climate Change (IPCC) guidelines include NO emissions during pasture renewal but do not consider NO emissions that may result from litter-fall. The objectives of this study were to determine litter-fall rates and to assess indicative NO emission factors (EFs) for the dominant pasture species (perennial ryegrass [ L.] and white clover [ L.]). Herbage was vacuumed from intensively managed dairy pastures before and after 30 different grazing events when cows (84 cows ha) grazed for 24 h according to a rotational system; the interval between grazing events ranged from 21 to 30 d. A laboratory incubation study was performed to assess potential EF values for the pasture species at two soil moisture contents. Finely ground pasture material was incubated under controlled laboratory conditions with soil, and the NO emissions were measured until rates returned to control levels. On average, pre- and postgrazing dry matter yields per grazing event were 2516 ± 636 and 1167 ± 265 kg DM ha (±SD), respectively. Pregrazing litter was absent, whereas postgrazing fresh and senesced litter-fall rates were 53 ± 24 and 19 ± 18 kg DM ha, respectively. Annually, the rotational grazing system resulted in 12 grazing events where fresh litter-fall equaed to 16 kg N ha yr to the soil. Emission factors in the laboratory experiment indicated that the EF for perennial ryegrass and white clover ranged from 0.7 to 3.1%. If such EF values should also occur under field conditions, then we estimate that litter-fall induces an NO emission rate of 0.3 kg NO ha yr. Litter-fall as a source of NO in grazed pastures requires further assessment.