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Fractional Atmospheric Nitrogen Loss From Tall Fescue Hay Spray-Irrigated With Municipal Wastewater Effluent
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| 자료유형 | 학위논문 |
|---|---|
| 서명/저자사항 | Fractional Atmospheric Nitrogen Loss From Tall Fescue Hay Spray-Irrigated With Municipal Wastewater Effluent. |
| 개인저자 | Sendagi, Stella Maris. |
| 단체저자명 | The Pennsylvania State University. Agricultural and Biological Engineering. |
| 발행사항 | [S.l.]: The Pennsylvania State University., 2017. |
| 발행사항 | Ann Arbor: ProQuest Dissertations & Theses, 2017. |
| 형태사항 | 271 p. |
| 기본자료 저록 | Dissertations Abstracts International 81-01B. Dissertation Abstract International |
| ISBN | 9781392335543 |
| 학위논문주기 | Thesis (Ph.D.)--The Pennsylvania State University, 2017. |
| 일반주기 |
Source: Dissertations Abstracts International, Volume: 81-01, Section: B.
Publisher info.: Dissertation/Thesis. Advisor: Elliott, Herschel A. |
| 요약 | Water reclamation and reuse through municipal wastewater effluent (MWE) irrigation reduces the pressure on global water resources and promotes environmental and human health protection. The design MWE irrigation rate is usually limited by the capacity of the soil to transmit water and nitrate (NO3-N) concentration in the percolate water. Nitrogen (N)-based irrigation depths (Ln) are often determined from an N mass balance, which requires estimation of the fractional N loss (f) due to atmospheric N losses through denitrification and ammonia (NH3) volatilization.Design f values are often chosen from the 0.15 to 0.25 range for secondary-treated effluents (C:N ratio = 0.9 to1.5) and 0.1 is suggested for tertiary-treated effluents (C:N ratio <0.9). A temperature-based guideline suggests an f value of 0.2 for "cold" climates and 0.25 for "warm" climates. However, no scientific investigations have verified these values. Design procedures could be improved if f estimates were replaced by empirically determined values. The overall goal of this research study was, therefore, to quantify f values over the growing season in an effluent-irrigated crop field. The f values were estimated using atmospheric N losses quantified using three approaches: measurements, model simulations, and "source-sink"혻N mass balances.The field study was completed in 2011 and 2012 at the Pennsylvania State University (PSU) Living Filter (LF) in a tall fescue grass field (8.4 ha) in Central Pennsylvania. The bulk density for the 0 to 12-cm depth of the surface soil horizon is 1.25 g cm-3, and the predominant soil series in the grass field is Hagerstown (fine, mixed, semiactive, mesic Typic Hapludalf) with loam and clay loam soil in the 0 to 30-cm depth of the surface soil horizon. The field is irrigated with secondary-treated effluent (including biological nitrogen removal) at a rate of 5 cm wk-1. Annual application of effluent N was 220 kg N ha-1 in 2011 and 153 kg N ha-1 in 2012, and on average, the effluent contained 70% and 87% NO3-N in 2011 and 2012, respectively. Supplemental N fertilizer was added as ureaammonium nitrate (30% N) (122 kg N ha-1 (2011) and 112 kg N ha-1 (2012)). In accordance with the 2006 USEPA design procedures for land treatment of municipal wastewater effluents, change in soil N storage was assumed to be negligible.Emissions of NH3 (gas) were measured in the field and laboratory with a photoacoustic field gas monitor immediately after effluent application. The maximum measured NH3 emission rate of 10-4 kg NH3-N ha-1 h-1 was roughly equivalent to 1 kg N ha-1 yr-1, which was insignificant relative to the effluent N applied during the study period. Thus, atmospheric N losses were mainly due to denitrification.The f values were estimated based on measured denitrification (fmd), simulated denitrification (fsd) and a monthly N mass balance (fnb). The fmd and fsd were estimated for twelve 7-day irrigation cycles. Denitrification gaseous fluxes (kg N ha-1 h-1) were measured from intact soil cores, collected from the surface soil horizon using 4.8 cm i.d. and 10.2 cm long aluminum cylinders, 6 to 7 h before irrigation (BI) began and 4 to 5 h after irrigation (AI) ceased. The cores were incubated in the laboratory for 6 h. Nitrous oxide concentrations in the core headspace were determined by gas chromatography. Daily denitrification fluxes were extrapolated from the hourly fluxes and the denitrification N loss per irrigation cycle (y) was estimated with the exponential equation y = ae-bx where x is the number of days after irrigation ceased. The constants a and b were determined using the AI and BI estimated daily denitrification fluxes.Denitrification was also simulated using the DeNitrificationDeComposition (DNDC) crop model. The model was parameterized in the site mode for four categories of simulations, namely: LD (DNDC default clay fraction = 0.19 and saturated hydraulic conductivity (Ksat) = 0.025 m h-1 for loam soil), CLD (DNDC default clay fraction = 0.4 and saturated hydraulic conductivity (Ksat) = 0.009 m h-1 for clay loam soil), LM (measured clay fraction = 0.26 and saturated hydraulic conductivity (Ksat) = 0.017 m h-1), and CLM (measured clay fraction = 0.31 and saturated hydraulic conductivity (Ksat) = 0.017 m h-1). (Abstract shortend by ProQuest.). |
| 일반주제명 | Soil sciences. Agricultural engineering. Environmental engineering. |
| 언어 | 영어 |
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