Nitrous oxide emission from wetland soil following single and seasonal split application of cattle manure to field tomato (Lycopersicon esculentum, Mill var. Heinz) and rape (Brassica napus, L. var. Giant) crops.

An understanding of the contribution of manure applications to global atmospheric N2O loading is needed to evaluate agriculture's contribution to the global warming process. Two field experiments were carried out at Dufuya wetland (19°17'S; 29°21'E, 1260 m above sea level) to determine the effects of single and split manure applications on emissions of N2O from soil during the growing seasons of two rape and two tomato crops. Two field experiments were established. In the first experiment the manure was applied in three levels of 0, 15, and 30 Mg ha(-1) as a single application just before planting of the first tomato crop. In the second experiment the 15 and 30 Mg ha(-1) manure application rates were divided into four split applications of 3.75 and 7.5 Mg ha(-1) respectively, for each of the four cropping events. Single applications of 15 and 30 Mg ha(-1) manure once in four cropping events had higher emissions of N2O than those recorded on plots that received split applications of 3.75 and 7.5 Mg ha(-1) manure at least up to the second test crop. Thereafter N2O emissions on plots subjected to split applications of manure were higher or equal to those recorded in plots that received single basal applications of 30 Mg ha(-1) applied a week before planting the first crop. Seasonal split applications of manure to wetland vegetable crops can reduce emissions of N2O at least up to the second seasonal split application.

Background

In sub-tropical regions of Africa, manures play an important role in soil fertility management through their short-term effects on nutrient supply and long-term contribution to the soil organic matter. The increasing prices of inorganic fertilizers coupled with growing concerns for sustaining soil productivity class="Chemical">has led to reclass="Chemical">newed iclass="Chemical">nterest iclass="Chemical">n the use of class="Chemical">n class="Species">cattle manures as fertility-restorer inputs (Mutsamba et al. 2012).

class="Chemical">Water is oclass="Chemical">ne of the most critical factors tclass="Chemical">n class="Chemical">hat limit smallholder crop production in the semi-arid areas of Zimbabwe. About 74 % of the smallholder areas of the country are located in the southern, western and central in Agro-ecological Regions III, IV and V, where rainfall is generally low and erratic (300–800 mm year−1) for reliable dry land cropping by smallholder farmers (Mugandani et al. 2012). The assured availability of water in wetlands which can be extracted without large capital intensive measures has enticed smallholder farmers to intensively utilize wetlands under cropping (Owen et al. 1995). The aerobically composted smallholder cattle manure remains the dominant fertilizer for use by the wetland farmers (Owen et al. 1995).

The addition of class="Species">cattle maclass="Chemical">nure to wetlaclass="Chemical">nd soil iclass="Chemical">ncreases the amouclass="Chemical">nt of readily decomposable orgaclass="Chemical">nic matter associated with high soil microbial activity (Markewich et al. 2010). This eclass="Chemical">nclass="Chemical">n class="Chemical">hances the potential for denitrification (Lin et al. 2011) and increased emissions of nitrous oxide (N2O) gas through a general stimulation of microbial respiration, causing rapid oxygen consumption and consequently an increase of anaerobic conditions (Yates et al. 2006; Jassal et al. 2011). Flooded soils in wetlands have aerobic and anaerobic zones, allowing both nitrification and denitrification to take place simultaneously (Johnson et al. 2005, Berdad-Haughn et al. 2006). Since the first process produces the substrate for the second, N losses can be very high when the two processes are associated (Snyder et al. 2009). As much as 60–70 % of applied N may be lost as N2O (Conrad et al. 1983; Markewich et al. 2010; Kamaa et al. 2011).

class="Chemical">Nitrous oxide is a greeclass="Chemical">nhouse aclass="Chemical">nd ozoclass="Chemical">ne-depleticlass="Chemical">ng gas (Mosier aclass="Chemical">nd Kroetze 1999; IPCC 2001; Vasileiadou et al. 2011; Mapaclass="Chemical">nda et al. 2012) whose atmospheric coclass="Chemical">nceclass="Chemical">ntratioclass="Chemical">n is curreclass="Chemical">ntly >310 class="Chemical">nL L−1 aclass="Chemical">nd iclass="Chemical">ncreasiclass="Chemical">ng at a rate of approximately 0.4 % per aclass="Chemical">nclass="Chemical">num (Mosier aclass="Chemical">nd Kroetze 1999). It is estimated to accouclass="Chemical">nt for some 6 % of the greeclass="Chemical">nhouse warmiclass="Chemical">ng (Ma et al. 2007). class="Chemical">n class="Chemical">Nitrous oxide has a global warming potential of 270–320 times compared to carbon dioxide (Snyder et al. 2009; Smith 2012). Nitrous oxide gas can last 150 years in the atmosphere (Munoz et al. 2010; Saggar 2010). The major sink for N2O is the stratospheric reaction with atomic oxygen to NO, which induces the destruction of stratospheric ozone. In addition, gaseous losses of manure N as N2O reduce the amount of N available to the crop and, therefore, its economic value as fertilizer (Lesschen et al. 2011). Several workers have reported that N2O is produced following the breakdown of N compounds in applied manures (Wrage et al. 2004; Wang et al. 2012; Smith 2012) in soil.

Research during the past several decades class="Chemical">has improved our uclass="Chemical">nderstaclass="Chemical">ndiclass="Chemical">ng of how class="Chemical">n class="Chemical">N2O is produced in agricultural systems, the factors that control its production, source/sink relationships, and gas movement processes. However, despite extensive knowledge of the processes involved, researchers are only beginning to be able to predict the fate of a unit of N that is applied or deposited on a specific agricultural field (Mosier et al. 2003). Existing data on emissions of N2O is extracted from research generated in western Europe, north America and south-east Asia (Kroetze et al. 2003) despite the fact that the tropics and subtropics contribute greatly to the emissions (Billy et al. 2010), particularly since 51 % of world soils are in these climate zones (Mosier et al. 2003). The incorporation of data on N2O emissions from African tropical and sub-tropical regions in the near future will lead to realistic and more appropriate emission factors being used by the IPCC (Kroetze et al. 2003). An understanding of the contribution of manure applications to global atmospheric N2O loading is needed to evaluate agriculture’s contribution to the global warming process (Mapanda et al. 2012). We report in this paper on two field experiments conducted over a period of two seasons in 2007 and 2008. The objective of this study was to quantify the effects of single and seasonal split applications of aerobically decomposed cattle manure on N2O fluxes from a wetland field during the growing seasons of rape and tomato crops under sub-tropical conditions in Zimbabwe. In this study it was hypothesized that the concentration of mineralized N in wetland soil, N2O emissions, N uptake and above ground dry matter yield of tomato and rape crops increase with increasing rates of application of aerobically composted cattle manure. It was also hypothesized that seasonal split applications of cattle manure in small doses reduces N2O fluxes in soil under rape (Brassica napus, L. var. Giant) and tomato (Lycopersicon esculentum, Mill var. Heinz).

Methods

Study site description

The study was conducted between 2007 and 2009 in a typical wetland garden at Dufuya (19°17′S; 29°21′E, 1260 m above sea level) wetlands in Chief Sogwala area of Lower Gweru Communal Lands, about 42 km west of the city of Gweru, Zimbabwe (Fig. 1).

Fig. 1

Study site location of Dufuya wetland in Zimbabwe

The field experimental site is in Agro-ecological Region III, which receives total rainfall ranging from 650 to 800 mm per annum (average 725 mm) and mean annual temperature is 21 °C with insignificant frost occurrence in the months of June and July (Mugandani et al. 2012). Rainfall occurs during a single rainy season extending from class="Chemical">November to April. The experimeclass="Chemical">ntal soil is a deeply weathered course textured loamy saclass="Chemical">nd topsoil over saclass="Chemical">ndy loam subsoil derived from graclass="Chemical">nite aclass="Chemical">nd classified as Udic Kaclass="Chemical">ndiustalf (USDA) aclass="Chemical">nd class="Chemical">n class="Chemical">Gleyic Luvisol (FAO) (FAO 1988; Nyamapfene; 1991 Soil Survey Staff 1992). The soil is perennially moist in part of the profile and smallholder farmers have established vegetable gardens along the wetland. Surface runoff and seepage of groundwater from catchment areas over an impermeable substratum towards lower lying areas, together with incident precipitation contribute largely to the water budget of the wetland. Vegetable production is all year round. The site had been under alternate rape, tomato, and maize crops for several years. Rape is cultivated as a leaf vegetable in Zimbabwe (De Lannoy 2001).

Characterization of experimental soil

Initial soil cclass="Chemical">haracterizatioclass="Chemical">n was doclass="Chemical">ne by collecticlass="Chemical">ng tweclass="Chemical">nty soil samples from raclass="Chemical">ndomly selected poiclass="Chemical">nts of the field experimeclass="Chemical">ntal site at a depth of 0–20 cm usiclass="Chemical">ng a soil auger. class="Chemical">n class="Chemical">Organic C in soil was determined using the Walkely and Black method (Nelson and Sommers 1996). Soil texture was determined by the Bouyocous hydrometer method (Bouyoucos 1965). Soil bulk density was determined by the core method (Black and Hartge 1986). The soil cores were oven-dried at 105 °C (to constant weight) for determination of mean gravimetric water content. Taking particle density (Pd) of soil to be 2.65 g cm−3 total porosity was calculated and recorded. Total N in soil was measured by the Kjeldahl method described by Bremner (1996). Results of the analyses are shown in Table 1.

Table 1

Chemical and physical properties of the experimental soil

Soil depth (cm)	Soil pH (H2O)	Org-C (%)	1N (mg kg−1)	Sand (%)	Clay (%)	Silt (%)	Total porosity (cm3 cm−3)	Bulk density (g cm−3)	Saturation gravimetric water (g g−1)
0–20	5.5	0.4	24	85	10	5	0.46	1.28	0.51
20–60	5.8	0.2	20	80	15	5	0.43	1.34	0.67
60–100	5.7	0.2	20	78	17	5	0.41	1.39	0.69

Land preparation and crop management

The land was prepared by digging using class="Chemical">haclass="Chemical">nd hoes to a depth of 30 cm aclass="Chemical">nd theclass="Chemical">n leveliclass="Chemical">ng usiclass="Chemical">ng a rake. Plots raised to a height of 15 cm, which measured 5 × 1.5 m, were theclass="Chemical">n carefully marked out. The distaclass="Chemical">nce betweeclass="Chemical">n the plots was 60 cm. Small 20 cm high ridges were established arouclass="Chemical">nd each plot to avoid cross-coclass="Chemical">ntamiclass="Chemical">natioclass="Chemical">n by surface ruclass="Chemical">n-off. class="Chemical">n class="Species">Tomato and rape crops were used as test crops in the study. The cropping sequence in the field experiment was: September–December 2007 first tomato, January–March 2008 first rape, April–July 2008 second tomato and September–November 2008 second rape crops. Spacing between rows was 30 and 15 cm within the rows for the rape crop. For the tomato crop the plant spacing was 90 cm between rows and 80 cm within rows.

Experimental manure

The smallholder farmers at Dufuya wetlands practice intensive class="Species">tomato aclass="Chemical">nd class="Chemical">n class="Species">rape production in small gardens under small scale irrigation (Owen et al. 1995). Because of lack of availability and higher cost of chemical fertilizers, the smallholder farmers have resorted to use of cattle manure which are readily available. The aerobically composted cattle manure used in the field plot experiment was collected from a homestead in the surrounding communal area. High rates of manure applications are used in order to avoid yield depression due to nutrient deficiency (Owen et al. 1995; De Lannoy 2001). Usually, 15 Mg ha−1 of cattle manure is applied by wetland farmers with limited number of cattle (<6). On average, 30 Mg cattle manure ha−1 is applied by wetland farmers with larger cattle herds (>6). Smallholder farmers in the wetland may apply these doses once in four cropping events because of the limited annual accumulations of manure in cattle holding pens. In some cases, smaller doses of cattle manure (3–8 Mg ha−1) in every cropping event are applied by farmers with a smaller herd of cattle. These manure application rates and seasonal split applications were used as treatments in the field experiments in order to capture the common farmer practice and test their effects on loss of N through N2O emissions.

Ten randomly selected samples were collected from a pile of manure and thoroughly mixed in a plastic bucket. Three replicate composite samples were taken for laboratory analysis. The samples were air-dried, passed through a 2 mm sieve, and analyzed for class="Chemical">organic C (class="Chemical">n class="Chemical">Nelson and Sommers 1982), total N using the Kjeidahl procedure (Bremner and Mulvaney 1982), soil, and ash content. Soil and ash contents were determined by ashing manure in a muffle furnace (450 °C) for 16 h. The ash was dissolved in concentrated HCl acid and separated from mineral soil by filtering. The soil was oven dried and weighed. The selected chemical properties of the experimental manure are shown in Table 2.

Table 2

Selected chemical properties of the smallholder cattle manure

Organic C (%)	Total N (%)	C:N ratio	Soil + ash content (%)	Soil and ash-free basis (%)
				Organic C	Total N
22.82	1.36	16.8:1	77.18	61.3	6.4

Selected chemical properties of the smallholder n class="Species">cattle maclass="Chemical">nure

Experimental design and treatments

Two experiments were used to determine the effect of manure application rates and seasonal split applications on n class="Chemical">N2O emissioclass="Chemical">n with three treatmeclass="Chemical">nts for each experimeclass="Chemical">nt:

Experiment 1:Experiment 2:

Control (unamended);

15 Mg manure n class="Chemical">ha−1 (applied oclass="Chemical">nce iclass="Chemical">n four successive class="Chemical">n class="Gene">cropping events);

30 Mg manure class="Chemical">N class="Chemical">n class="Chemical">ha−1 (applied once in four successive cropping events).

Control (unamended);

15 Mg manure n class="Chemical">ha−1 (iclass="Chemical">n four seasoclass="Chemical">nal split applicatioclass="Chemical">ns);

30 Mg manure n class="Chemical">ha−1 (iclass="Chemical">n four seasoclass="Chemical">nal split applicatioclass="Chemical">ns).

A randomized complete block design with four replications was employed. The blocking factor was the slope gradient. In Experiment 1, the 15 and 30 Mg manure class="Chemical">ha−1 were applied oclass="Chemical">nce iclass="Chemical">n four class="Chemical">n class="Gene">cropping events in the respective plots by broadcasting on the surface and then incorporating into the soil just before transplanting the first tomato crop. In Experiment 2, the 15 and 30 Mg ha−1 manure rates, applications were divided into four split seasonal applications over the study period in which two tomato and two rape crops were planted. For the 15 Mg ha−1 cattle manure treatments, the first application of 3.75 Mg ha−1 was done by evenly applying manures in planting rows on the raised plots and then incorporating it a few days before planting the first tomato crop. The balance of three applications of 3.75 Mg ha−1 was applied to each of the remaining three crops in the study by applying into the planting furrows and covering with soil before planting each crop. The same seasonal split application procedure was repeated for the 30 Mg ha−1 manure treatments, which was divided into four applications of 7.5 Mg ha−1 for each of the four crops.

A bclass="Chemical">asal applicatioclass="Chemical">n rate of 1000 kg class="Chemical">n class="Chemical">ha−1 compound S (5 % N, 7.9 % P, 16.6 % K, and 8 % S) was used in all treatments before planting each crop to capture common fertilizer application practice at Dufuya wetland.

Weather conditions

Rainfall data were collected daily at 10.00 h from a rain gauge at the study site. Maximum and minimum daily temperatures at the study site were gap-filled using the department of Agricultural Technical and Extension Services (n class="Chemical">AGRITEX) meteorological data at Sogwala (19°17′S; 29°21′E) rural service ceclass="Chemical">ntre located 2 km west of the study site. The meteorological statioclass="Chemical">n records daily weather data (Fig. 2).

Fig. 2

Daily rainfall, air temperature at the study site

Static chamber set-up and N2O flux measurement

class="Chemical">Nitrous oxide emissioclass="Chemical">ns from soil were trapped usiclass="Chemical">ng static cclass="Chemical">n class="Chemical">hamber method described by Holland et al. (1999) and Meyer et al. (2001). There were seven gas sampling campaigns at 14 day interval for the tomato crop. Six gas sampling events were performed at 14 day interval for the rape crop. Gas sampling was done at time 0 min to obtain the start values of atmospheric concentration of N2O in the static chamber head space and after 30 and 60 min (Mathias et al. 1980; Kaiser et al. 1996). The gas samples were analyzed for N2O concentration by means of a Varian Model 3400 gas chromatograph (Walnut Creek, CA, USA) as described by Mosier and Mack (1980) and Galle et al. (2003). Nitrous oxide fluxes (Fn) were calculated using the Hutchinson and Livingston (1993) model:where is the rate of change in N2O concentration (µmol mol−1 min−1), V is the chamber headspace volume (m3), Mn is the molecular weight of N2O (44 g mol−1), A is the surface area (m2) and Vmol is the volume of 1 mol of gas at 20 °C (0.024 m3 mol−1). Further conversions were performed to calculate Fn fluxes in g ha−1 day−1 as follows (Eq. 2):

Total class="Chemical">N lost as class="Chemical">n class="Chemical">N2O (N kg ha−1) was calculated using Eq. 3:where T is the number of days with similar daily N2O emissions rates and 28/44 is the conversion ratio for converting N2O molar mass to N content.

Soil mineral N measurements

At the same time tclass="Chemical">hat gas samples were collected, soil samples (class="Chemical">n = 4 per plot) were also collected from the plots aclass="Chemical">nd aclass="Chemical">nalyzed for class="Chemical">n class="Chemical">NH4-N and NO3-N. The soil samples were collected from a depth of 0 to 20 cm using a soil auger. Both analyses were performed using an Alpkem 3550 Flow Injector Analyzer (01 Analytical, College Station, TX, USA) using colorimetric techniques (Robertson et al. 1999).

Dry matter yield

Four randomly selected plants were chosen and labeled in each plot for class="Gene">crop biomass sampliclass="Chemical">ng. All class="Chemical">n class="Species">rape leaves and tomato fruits that reached horticultural maturity were harvested from the selected plants at every harvesting event and taken to the laboratory. The samples were rinsed; oven dried at 65 °C for 24 h and kept in a dry place. At the end of the growing season, the aboveground biomass of the selected plants was summed up. The composite samples were then ground to pass a 2 mm sieve and analyzed for N concentration semi-micro Kjeldahl procedure (Bremner and Mulvaney 1982). Total uptake of N was determined by multiplying the N concentration with dry matter yield as follows (Eq. 4):where [N] is content of N in mg g−1 dry matter and DM is dry matter yield in T ha−1.

Mineralized class="Chemical">N coclass="Chemical">nceclass="Chemical">ntratioclass="Chemical">ns iclass="Chemical">n soil were moclass="Chemical">nitored at 2-week iclass="Chemical">nterclass="Chemical">nals for each treatmeclass="Chemical">nt aclass="Chemical">nd estimated over 98 aclass="Chemical">nd 84 days for class="Chemical">n class="Species">tomato and rape crops respectively.

Statistical analysis

Treatment effects on measured variables in each experiment were analyzed using one way Aclass="Chemical">NOVA (Geclass="Chemical">nStat Discovery Editioclass="Chemical">n 3 2003; Geclass="Chemical">nStat VSclass="Chemical">n class="Chemical">NI 2011). Differences between treatment means were judged significant at p ≤ 0.05 as determined by Fisher’s protected least significant difference (LSD) test. Flux data were log-transformed to normalize the distributions before the statistical analysis. Mean separation was performed using the LSD since there were not >3 treatments in each set of experiment. Statistical significance of the differences between measured variables in plots subjected to single and seasonal split manure applications was established by performing t test for unpaired samples using the GenStat package. The Pearson coefficients of determination between measured variables and their r2 values were computed using Microsoft Excel. Significance of correlations between selected variables was established using a linear model GenStat analysis of correlation at 5 % level.

Results

NH4-N concentrations in soil following single and split application of manure

The concentration of class="Chemical">NH4-N iclass="Chemical">n soil subjected to siclass="Chemical">ngle applicatioclass="Chemical">n was sigclass="Chemical">nificaclass="Chemical">ntly (p < 0.05) higher tclass="Chemical">n class="Chemical">han that in soil subjected to seasonal split applications during the growing period of the first tomato and rape crops (Fig. 3a, b). However, only rates of manure applications had a significant (p < 0.05) effect on the differences in the concentrations of NH4-N during the growing seasons of the second tomato and rape crops. The effect of single and split application of cattle manure on NH4-N concentration was not significant (p > 0.05) during the growing period of the second tomato and rape crops (Fig. 3c, d). Except for the first rape crop, NH4-N concentrations decreased steadily towards the end of the growing period for each crop.

Fig. 3

NH4-N concentration in wetland soil following single and split application of manure. app application. a First tomato crop, b first rape crop, c second tomato crop and d second rape crop

class="Chemical">NH4-N coclass="Chemical">nceclass="Chemical">ntratioclass="Chemical">n iclass="Chemical">n wetlaclass="Chemical">nd soil followiclass="Chemical">ng siclass="Chemical">ngle aclass="Chemical">nd split applicatioclass="Chemical">n of maclass="Chemical">nure. app applicatioclass="Chemical">n. a First class="Chemical">n class="Species">tomato crop, b first rape crop, c second tomato crop and d second rape crop

Single applications of 15 Mg of manure increased the concentration of class="Chemical">NH4-N iclass="Chemical">n soil by 2.3 (30 %) aclass="Chemical">nd 2.0 mg kg−1 soil (27 %) above those recorded oclass="Chemical">n plots ameclass="Chemical">nded with the first aclass="Chemical">nd secoclass="Chemical">nd split applicatioclass="Chemical">n of 3.75 Mg maclass="Chemical">nure class="Chemical">n class="Chemical">ha−1 for the first tomato and rape crops, respectively. Single applications of 30 Mg manure ha−1 increased NH4-N concentration in soil by 2.9 (29 %) and 2.3 mg kg−1 soil (21 %) above those recorded in plots subjected to the first and second split 7.5 Mg ha−1 manure applications for the first tomato and rape crops.

NO3-N concentration in soil following single and split application of manure

Trends for class="Chemical">NO3-N aclass="Chemical">nd class="Chemical">n class="Chemical">NH4-N concentrations in soil were comparatively similar during the growing period of test crops. Effects of single and split applications of manure on NO3-N were significant (p < 0.05) only up to the second split application while their effects became insignificant (p > 0.05) in the third and fourth split applications (Fig. 4).

Fig. 4

NO3-N concentration in wetland soil follow ing single and split application of manure. app application. a First tomato crop, b first rape crop, c second tomato crop and d second rape crop

class="Chemical">NO3-N coclass="Chemical">nceclass="Chemical">ntratioclass="Chemical">n iclass="Chemical">n wetlaclass="Chemical">nd soil follow iclass="Chemical">ng siclass="Chemical">ngle aclass="Chemical">nd split applicatioclass="Chemical">n of maclass="Chemical">nure. app applicatioclass="Chemical">n. a First class="Chemical">n class="Species">tomato crop, b first rape crop, c second tomato crop and d second rape crop

Generally, there were significant temporal variations in the concentrations of class="Chemical">NO3-N iclass="Chemical">n soil from placlass="Chemical">nticlass="Chemical">ng up to the cessatioclass="Chemical">n of the growiclass="Chemical">ng period of each vegetable class="Chemical">n class="Gene">crop. Application of 15 Mg ha−1 manure once in four cropping events significantly increased (p < 0.05) the content of NO3-N in wetland soil by 2.4 (40 %) and 1.6 mg kg−1 soil (27 %) above those recorded on plots amended with the first and second split application of 3.75 Mg manure ha−1 for the first tomato and rape crops.

Single applications of 30 Mg manure class="Chemical">ha−1 sigclass="Chemical">nificaclass="Chemical">ntly (p < 0.05) iclass="Chemical">ncreased class="Chemical">n class="Chemical">NO3-N concentrations in soil by 2.4 (27 %) and 1.8 mg kg−1 soil (21 %) above those recorded in plots amended with first and second split 7.5 Mg ha−1 manure for the first tomato and rape crops, respectively. When a single application of 15 and 30 Mg ha−1 manure were used instead of 3.75 and 7.5 Mg ha−1 applied as a third split application mean NO3-N concentration differences between the two treatments approached similar levels and were insignificant in the second tomato and rape crops (third and fourth split applications). The mean differences in the concentrations of NO3-N in wetland soil between plots amended with single applications at the beginning of the experiment and split applications before planting the successive test crops progressively became narrower towards the end of the experiment.

Nitrous oxide fluxes from soil following single and split application of manure

Results show tclass="Chemical">hat the rate of class="Chemical">n class="Species">cattle manure applications exerted significant differences (p < 0.05) in N2O fluxes following single and seasonal split manure applications throughout the study period (Fig. 5). Nevertheless, split application of manure exerted significant (p < 0.05) effect on N2O emissions within the growing periods of the first tomato and rape crops only (Fig. 4a, b) when compared with the control.

Fig. 5

N2O fluxes from wetland soil following single and split application of manure. app application. a First tomato crop, b first rape crop, c second tomato crop and d second rape crop

class="Chemical">N2O fluxes from wetlaclass="Chemical">nd soil followiclass="Chemical">ng siclass="Chemical">ngle aclass="Chemical">nd split applicatioclass="Chemical">n of maclass="Chemical">nure. app applicatioclass="Chemical">n. a First class="Chemical">n class="Species">tomato crop, b first rape crop, c second tomato crop and d second rape crop

Considerably higher class="Chemical">N2O emissioclass="Chemical">ns were observed iclass="Chemical">n the first gas samples collected from vegetable plots ameclass="Chemical">nded with siclass="Chemical">ngle applicatioclass="Chemical">ns of 30 Mg class="Chemical">n class="Chemical">ha−1 manure, which was applied a week before planting the first tomato crop. In single manure applications, elevated N2O fluxes persisted throughout the 98 and 84-day period for tomato and rape crops respectively. In split applications of manure, N2O fluxes remained constant or gradually decreased despite additions of cattle manure before each planting event.

Single applications of 15 Mg manure class="Chemical">ha−1 iclass="Chemical">ncreased class="Chemical">n class="Chemical">N2O fluxes by 1.8 (36 %) and 2.7 g ha−1 day−1 (43 %) above those recorded from plots subjected to the first and second split application of 3.75 Mg manure ha−1 applied a week before planting the first crop for the tomato and rape crops, respectively. The same practice at 30 Mg manure ha−1 application levels increased N2O fluxes on wetland soil by 2.5 (38 %) and 3.1 g ha−1 day−1 (34 %).

Soil factors–N2O emission relationships

The concentrations of class="Chemical">NH4-N aclass="Chemical">nd class="Chemical">n class="Chemical">NO3-N in soil are important predictors of N2O fluxes in soil (Figs. 6, 7). Regression analysis between measured variables after split and single application of cattle manure are shown in Figs. 6 and 7. Results show significant correlations (p < 0.05) between NO3-N; NH4-N; soil moisture and emissions of N2O. Coefficients of regression in the correlations between soil moisture and N2O emissions varied between 0.26 and 0.69 (Figs. 6e, f, 7a, b). The coefficients of regression (r2) values for the positive linearity in the relationships between NH4-N concentrations in soil and N2O emissions ranged from 0.42 to 0.78 after split and single manure application. The coefficients of determination in the relationships between NO3-N in soil and N2O fluxes on soil varied between 0.47 and 0.77. The r2 values the relationships between NH4-N, NO3-N in soil and emissions of N2O were comparatively similar.

Fig. 6

Regression analyses showing relationships between mineral N, N2O and wetland soil moisture after split application of manure

Fig. 7

Regression analyses showing relationships between mineral N, N2O and wetland soil moisture after a single application of manure

Regression analyses showing relationships between mineral class="Chemical">N, class="Chemical">n class="Chemical">N2O and wetland soil moisture after split application of manure

Regression analyses showing relationships between mineral class="Chemical">N, class="Chemical">n class="Chemical">N2O and wetland soil moisture after a single application of manure

Aboveground dry matter yield and N uptake following split and single application of manure

Dry matter yield and class="Chemical">N uptake followiclass="Chemical">ng seasoclass="Chemical">nal split aclass="Chemical">nd siclass="Chemical">ngle applicatioclass="Chemical">n of maclass="Chemical">nure are showclass="Chemical">n iclass="Chemical">n Tables 3 aclass="Chemical">nd 4. The effects of siclass="Chemical">ngle aclass="Chemical">nd split applicatioclass="Chemical">ns of maclass="Chemical">nure oclass="Chemical">n class="Chemical">n class="Chemical">N uptake were significant (p < 0.05) for all vegetable crops. However, the differences in dry matter yield between plots subjected to single applications and those amended with the first split applications were larger than those recorded between single manure applied plots and the plots amended with the fourth split application of manure.

Table 3

Aboveground dry matter yield and N uptake after split application of manure

Trts	First tomato			First rape			Second tomato			Second rape
	DM yield T ha−1	mg N g−1 DM	N uptake (kg ha−1)	DM yield (T ha−1)	mg N g−1 DM	N uptake (kg ha−1)	DM yield (T ha−1)	mg N g−1 DM	N uptake (kg ha−1)	DM yield (T ha−1)	mg N g−1 DM	N uptake (kg ha−1)
T1	3	9.8	29.3	9.9	1.6	14.9	3.1	12.9	40.3	10.5	2.9	29.9
T2	3.3	10.4	33.6	11.2	2.9	32.8	4	15.5	62.0	13.3	6.2	82.8
T3	3.6	14.1	50.6	12.7	7.7	98.0	5.8	17	100.2	15	9.9	148.5
Fpr	*	*	*	*	*	*	*	*	*	*	*	*
LSD (5 %)	0.1	3	3.9	0.2	0.2	1.4	0.1	2.3	2.7	0.2	0.5	5.6
CV %	0.9	15.3	5.9	1.2	2.7	1.6	1.8	10.4	2.3	1	4.2	4.5

T1—control, T2—15 Mg high N manure ha−1 split into four 3.75 Mg ha−1 per crop, T3—30 Mg high N manure ha−1 split into four 7.5 Mg ha−1 per crop, DM—dry matter yield, mg N g−1 DM—milligrams of N per gram dry matter

* p > 0.05

Table 4

Dry matter yield and N uptake by aboveground plant biomass following single application of manure

Trts	First tomato (2007–2008)			First rape (2008–2009)			Second tomato (2008–2009)			Second rape (2008–2009)
	DM yield (T ha−1)	mg N g−1 DM	N uptake (kg ha−1)	DM yield (T ha−1)	mg N g−1 DM	N uptake (kg ha−1)	DM yield (T ha−1)	mg N g−1 DM	N uptake (kg ha−1)	DM yield (T ha−1)	mg N g−1 DM	N uptake (kg ha−1)
T1	3.0	7.0	20.9	10.5	1.5	9.1	3.1	9.1	28.2	10.1	2.2	32.3
T2	5.5	11.7	79.6	12.0	4.6	57.5	7.0	7.1	55.7	11.0	3.2	59.2
T3	8.5	17.2	146.2	16.5	8.5	136.2	9.5	16.1	138.2	16.5	5.8	121.8
Fpr	*	*	*	*	*	*	*	*	*	*	*	*
LSD (5 %)	0.1	0.8	0.7	1.4	1.3	0.5	0.5	1.6	1.2	1.0	1.2	0.6
CV %	1.0	4.1	5.3	6.2	15.4	5.4	4.2	6.6	7.4	3.8	12.4	6.8

Trts—treatments, T1—control, T2—15 Mg manure ha−1 applied once in four cropping events, 30 Mg high N manure ha−1 applied once in four cropping events, DM—dry matter yield, mg N g−1 DM—milligrams of N per gram dry matter

Aboveground dry matter yield and n class="Chemical">N uptake after split applicatioclass="Chemical">n of maclass="Chemical">nure

T1—control, T2—15 Mg high class="Chemical">N maclass="Chemical">nure class="Chemical">n class="Chemical">ha−1 split into four 3.75 Mg ha−1 per crop, T3—30 Mg high N manure ha−1 split into four 7.5 Mg ha−1 per crop, DM—dry matter yield, mg N g−1 DM—milligrams of N per gram dry matter

Dry matter yield and n class="Chemical">N uptake by abovegrouclass="Chemical">nd placlass="Chemical">nt biomass followiclass="Chemical">ng siclass="Chemical">ngle applicatioclass="Chemical">n of maclass="Chemical">nure

Trts—treatments, T1—control, T2—15 Mg manure class="Chemical">ha−1 applied oclass="Chemical">nce iclass="Chemical">n four class="Chemical">n class="Gene">cropping events, 30 Mg high N manure ha−1 applied once in four cropping events, DM—dry matter yield, mg N g−1 DM—milligrams of N per gram dry matter

class="Chemical">N uptake was lowest iclass="Chemical">n the coclass="Chemical">ntrol plots aclass="Chemical">nd highest iclass="Chemical">n plots tclass="Chemical">n class="Chemical">hat received 30 Mg manure as a single application. Plots amended with split applied manure recorded substantial reductions in N uptake when compared with those recorded on plots amended with single manure applications. When 15 and 30 Mg manure ha−1 were applied once, N uptake increased by 48.3 kg ha−1 or 59 % and 102 kg N ha−1 or 67 % in excess of those recorded in plots amended with the first split applications of 3.75 and 7.5 Mg manure ha−1, respectively.

The second class="Species">tomato class="Chemical">n class="Gene">crop experienced increase of N uptake of 63.4 kg ha−1 or 51 % and 76.0 kg ha−1 or 43 % in plots subjected to single applications of 15 and 30 Mg manure ha−1 in comparison with those observed in plots amended with the third split applications of 3.75 and 7.5 Mg manure ha−1 respectively.

While class="Chemical">N uptake respoclass="Chemical">nses to siclass="Chemical">ngle applicatioclass="Chemical">ns of 15 aclass="Chemical">nd 30 Mg high class="Chemical">n class="Chemical">N manure ha−1 were 37–67 % above those in plots subjected to split applications of 3.75 and 7.5 Mg manure ha−1 for the three previous crops, the same soil fertilization practice could increase N uptake by only 3.4 kg ha−1 or 4 % and 10.5 kg ha−1 or 7 % respectively for the last crop in the study.

Single applications of high class="Chemical">N maclass="Chemical">nure at 15 Mg class="Chemical">n class="Chemical">ha−1 stimulated an increase of 51, 11, 42, and 19 % in dry matter yield in excess of those recorded on plots subjected to the first, second, third and fourth split applications of high N manure. The application of 30 Mg manure ha−1 once during the study period caused an increase in dry matter yield of 58, 23, 23, and 9 % during the first, second, third and fourth split application of 7.5 Mg ha−1 manure.

Total N lost as nitrous oxide

Tables 5 and 6 shows estimated losses of class="Chemical">N iclass="Chemical">n class="Chemical">n class="Chemical">N2O emission after seasonal split and single applications of manure to rape and tomato crops. Single applications of cattle manure had a significant effect on losses of N2O from soil throughout the growing period of tomato and rape crops (Table 4). The effect of split applications of manure on emissions of N2O were significant (p < 0.05) during the growing period of the first tomato and rape crops only (Table 3). Thereafter, the rates of application rather than the factors of single and seasonally split manure applications had significant effect on total N lost through N2O emissions. Losses of N through N2O emission on plots amended with split applications of manure were 23–138 % above the losses recorded on the control plots. Estimated total N lost through N2O emissions on plots subjected to single applications of manure were 121 and 134 % above the emissions recorded on control plots. Amongst the manure amended plots, lower N losses of N2O emission were recorded in the second tomato, a crop which grew under dry weather conditions of the 2008 April–July winter season.

Table 5

Estimated total N lost through nitrous oxide emission following seasonal split application of manure

Trts	First tomato crop					First rape crop
	Temporal interval (days after planting)	Mean rate of N2O emission (g ha−1 day−1)	Total N emitted for the period (kg ha−1)	Total N applied (kg ha−1)	% emitted N2O of applied N	Temporal interval (days after planting)	Mean rate of N2O emission (g ha−1 day−1)	Total N emitted for the period (kg ha−1)	Total N applied (kg ha−1)	% emitted N2O of applied N
T1	1–21	5.4	0.11	–	–	1–49	6.0	0.30	–	–
	22–49	2.5	0.07	–	–	50–84	3.9	0.13	–	–
	50–63	2.8	0.04	–	–	–	–	–	–	–
	64–98	6.4	0.22	–	–	–	–	–	–	–
Total			0.44	0	0	–	–	0.43	0	0
T2	1–21	5.6	0.12	–	0.24	1–49	9.3	0.45	–	0.88
	22–49	5.7	0.15	–	0.29	50–84	4.6	0.15	–	0.29
	50–63	5.7	0.07	–	0.14	–	–	–	–	–
	64–98	7.2	0.24	–	0.47	–	–	–	–	–
Total	–	–	0.58	51	1.14	–	–	0.60	51	1.18
T3	1–21	7.5	0.15	–	0.15	1–49	12.7	0.62	–	0.61
	22–49	6.8	0.16	–	0.16	50–84	7.2	0.24	–	0.24
	50–63	6.5	0.08	–	0.08	–	–	–	–	–
	64–98	9.4	0.31	–	0.15	–	–	–	–	–
Total	–	–	0.70	102	0.69	–	–	0.86	102	0.84
Fpr	–	–	*	–	–	–	–	*	–	–
LSD	–	–	0.16	–	–	–	–	0.23	–	–
CV	–	–	13.40	–	–	–	–	12.20	–	–

Trt—treatments, T1—control, T2—15 Mg high N manure ha−1 split into four 3.75 Mg ha−1 applications per crop, T3—30 Mg high N manure ha−1 split into four 7.5 Mg ha−1 applications per crop

* p > 0.05

Table 6

Estimated total N lost through N2O emission following single application of manure

Trts	First tomato crop					First rape crop
	Temporal interval (days after planting)	Mean rate of N2O emission (g ha−1 day−1)	Total N emitted for the period (kg ha−1)	Total N applied (kg ha−1)	% emitted N2O of applied N	Temporal interval (days after planting)	Mean rate of N2O emission (g ha−1 day−1)	Total N emitted for the period (kg ha−1)	Total N applied (kg ha−1)	% emitted N2O of applied N
T1	1–21	5.6	0.12	–	–	1–49	6.0	0.30	–	–
	22–49	2.4	0.07	–	–	50–84	3.9	0.13	–	–
	50–63	2.7	0.04	–	–	–	–	–	–	–
	64–98	6.0	0.21	–	–	–	–	–	–	–
Total			0.44	0	0	–	–	0.43	0	0
T2	1–21	8.1	0.17	–	0.08	1–49	10.1	0.50	–	0
	22–49	7.1	0.19	–	0.09	50–84	5.8	0.40	–	0
	50–63	7.0	0.09	–	0.04	–	–	–	–	–
	64–98	9.1	0.31	–	0.15	–	–	–	–	–
Total	–	–	0.76	204	0.37	–	–	0.90	0	0
T3	1–21	13.5	0.28	–	0.07	1–49	14.1	0.70	–	0
	22–49	9.0	0.24	–	0.06	50–84	10.1	0.30	–	0
	50–63	8.0	0.10	–	0.02	–	–	–	–	–
	64–98	10.3	0.35	–	0.09	–	–	–	–	–
Total	–	–	0.97	408	0.24	–	–	1.00	0	0
Fpr	–	–	*	–	–	–	–	*	–	–
LSD	–	–	0.16	–	–	–	–	0.23	–	–
CV	–	–	13.40	–	–	–	–	12.20	–	–

Trts—treatments, T1—control, T2—15 Mg high N manure ha−1, T3—30 Mg high N manure ha−1

* p > 0.05

Estimated total class="Chemical">N lost through class="Chemical">n class="Chemical">nitrous oxide emission following seasonal split application of manure

Trt—treatments, T1—control, T2—15 Mg high class="Chemical">N maclass="Chemical">nure class="Chemical">n class="Chemical">ha−1 split into four 3.75 Mg ha−1 applications per crop, T3—30 Mg high N manure ha−1 split into four 7.5 Mg ha−1 applications per crop

Estimated total class="Chemical">N lost through class="Chemical">n class="Chemical">N2O emission following single application of manure

Trts—treatments, T1—control, T2—15 Mg high class="Chemical">N maclass="Chemical">nure class="Chemical">n class="Chemical">ha−1, T3—30 Mg high N manure ha−1

When 15 Mg class="Chemical">ha−1 of maclass="Chemical">nure were applied oclass="Chemical">nce iclass="Chemical">n the four class="Chemical">n class="Gene">cropping events N2O emission increased by 31 and 38 % above those recorded from plots subjected to the first and second split application of 3.75 Mg manure ha−1 applied a week before planting the first tomato and rape crops, respectively. Mean differences in total N lost as N2O emission between plots amended with a single basal application of 30 Mg of manure and those amended with the first and second seasonally split application of 7.5 Mg manure ha−1 were 39 and 13 % for the first tomato and rape crops respectively. As the study approached the last cropping event, mean differences in the loss of N through N2O emissions between plots amended with single basal applications and those that received seasonally split applications became progressively smaller and insignificant.

When 15 and 30 Mg manure class="Chemical">ha−1 were applied oclass="Chemical">nce iclass="Chemical">n four class="Chemical">n class="Gene">cropping events 0.4 and 0.9 % of applied N was lost as N2O, respectively, during the growing period of the first tomato crop. When 15 and 30 Mg of manure were split applied into four applications of 3.75 and 7.5 Mg ha−1 to every crop total N losses in N2O emission represented 0.9 and 0.9 % (for the rape crop); 0.8 and 0.6 % (for the tomato crop) of applied N. Generally, the proportion of applied N lost as N2O was higher in the rape crop than in the tomato crop.

Total N lost in N2O emission per unit dry matter

Table 7 shows class="Chemical">N lost iclass="Chemical">n class="Chemical">n class="Chemical">N2O emission per unit of harvested dry matter yield after the single application of cattle manure in four vegetable cropping events. When the application rates of manure were increased from 15 to 30 Mg ha−1, the emissions of N2O per unit harvested dry matter of rape and tomato significantly decreased (p < 0.05). The estimated loss of N in N2O emissions decreased by 0.01–0.03 and 0.01–0.06 kg N-N2O per T of harvested dry matter when manure application rates were increased from 15 to 30 Mg ha−1, respectively. Nitrous oxide emission losses per unit harvested dry matter of tomato crop were significantly (p < 0.05) higher in the unamended plots than on manure fertilized plots (Table 7). However, losses of N in N2O emissions per unit harvested dry matter from the control plots under rape crop were generally lower when compared with the losses from manure fertilized plots.

Table 7

Estimated N lost in N2O emission per unit dry matter yield after single manure application

Trts	First tomato			First rape			Second tomato			Second rape
	DM yield (T ha−1)	N emitted in N2O (kg ha−1)	kg N emitted per T DM	DM yield (T ha−1)	N emitted in N2O (kg ha−1)	kg N emitted per T DM	DM yield (T ha−1)	N emitted in N2O (kg ha−1)	kg N emitted per T DM	DM yield (T ha−1)	N emitted in N2O (kg ha−1)	kg N emitted per T DM
T1	3.0	0.44	0.15	10.5	0.43	0.04	3.1	0.32	0.10	10.1	0.33	0.03
T2	5.5	0.76	0.14	12.0	0.90	0.08	7.0	0.51	0.07	11.0	0.65	0.06
T3	8.5	0.97	0.11	16.5	1.00	0.06	9.5	0.60	0.06	16.5	0.75	0.05
Fpr	*	*	*	*		*	*	*	*	*	*	*
LSD (5 %)	0.1	0.17	0.01	0.2	0.21	0.01	2.5	0.07	0.01	0.4	0.10	0.01
CV%	10.8	5.3	1.8	1.0	3.8	9.6	24.6	7.1	3.2	1.7	5.2	4.1

Trts—treatments, DM—dry matter, T1—0 Mg ha−1 manure (control), T2—15 Mg ha−1 manure, T3—30 Mg ha−1 manure

* p < 0.05

Estimated class="Chemical">N lost iclass="Chemical">n class="Chemical">n class="Chemical">N2O emission per unit dry matter yield after single manure application

Trts—treatments, class="Disease">DM—dry matter, T1—0 Mg class="Chemical">n class="Chemical">ha−1 manure (control), T2—15 Mg ha−1 manure, T3—30 Mg ha−1 manure

Discussion

Effect of seasonal split and single manure application on soil mineral N and N2O emission

Wetland smallholder farmers in subtropical Africa commonly apply manure in small doses in each vegetable class="Gene">croppiclass="Chemical">ng eveclass="Chemical">nt while others apply large doses oclass="Chemical">nce iclass="Chemical">n 3–4 class="Chemical">n class="Gene">cropping occasions. Results in this study have clearly demonstrated that small dose manure application per crop can only reduce losses of N by gaseous emissions of N2O at least up to the second cropping event. This trend in the N2O flux responses to the treatments clearly suggested that the single applications of 15 and 30 Mg manure ha−1 provided substantially higher masses of organic substrate (Markewich et al. 2010) for the microbial degradation processes in aerated macro-pores of the soil profile during the first two vegetable cropping events. In studies related to N transformations in soils Markewich et al. (2010) reported significant accumulations of mineralized N (NH4-N and NO3-N) in microbially driven organic matter decomposition. Upon flooding of the macro-pores with soil water in the wetland (Johnson et al. 2005; Berdad-Haughn et al. 2006) some of the NO3-N is subjected to denitrification (Ma et al. 2007) associated with emissions of N2O in soil. In addition to that, the application of cattle manure to wetland soil enhances its potential for emissions of N2O gas by stimulating increased microbial respiration, causing rapid oxygen consumption and consequently an increase of anaerobic conditions for the onset of denitrification processes (Yates et al. 2006; Jassal et al. 2011). Wetland soils have aerobic and anaerobic sites that allow nitrification and denitrification to take place simultaneously (Johnson et al. 2005). Since the first process produces the substrate for the second, N losses through emissions of N2O can be high when the two processes are associated (Snyder et al. 2009). Evidently, the application of cattle manure to wetland cropping systems has the potential of increasing the contribution of agriculture to atmospheric N2O loading (Markewich et al. 2010; Kamaa et al. 2011).

The mean differences in the rates of class="Chemical">N2O emissioclass="Chemical">ns betweeclass="Chemical">n plots ameclass="Chemical">nded with siclass="Chemical">ngle bclass="Chemical">n class="Chemical">asal applications and those that received split applications became progressively smaller and insignificant (p > 0.05) towards the last test crop. The decline in the vegetable plots that received single basal manure applications in evolving elevated amounts of N2O over those that received seasonal split manure amendments is attributed to the rapid decrease in the capacity of the plots that received single manure amendments to supply NO3-N, which is a substrate for the microbes that participate in the denitrification process. This decline in the content of mineralised N is a consequent of successive N uptake without replenishments, immobilization in ligno-protein complexes of humus formation (Yates et al. 2006), N2O gas evolving denitrification (Kamaa et al. 2011; Lesschen et al. 2011), and migration of NO3-N to ground water resources (Mapanda et al. 2012).

Results from the regression analysis implied tclass="Chemical">hat soil miclass="Chemical">neral class="Chemical">n class="Chemical">N concentrations (NH4-N and NO3-N) displayed significant (p < 0.05) influence on the variability found in N2O emission. Both processes of nitrification of NH4-N and denitrification of NO3-N are thought to contribute immensely to the emissions of N2O although the later has been suggested to play a bigger role in the emissions (Ma et al. 2007; Smith 2012). In this study, NH4-N and NO3-N exerted comparatively equal influence on the variability found in N2O emissions in surface soil (r2 = 0.51–0.55 vs. 0.52–0.53 for first tomato crop; r2 = 0.51–0.57 vs. 0.50–0.53 for first rape crop; r2 = 0.42–0.78 vs. 0.47–0.77 for second tomato crop; r2 = 0.51–0.52 vs. 0.52–0.54 for second rape crop). The first stage in the decomposition of N-containing organic materials in applied manure produces ammoniacal N which is a substrate for the second process involving nitrification. Nitrogen losses in N2O emissions can be very high when the two processes are associated. As much as 60–70 % of fertilizer N applied to wetland crop may be volatilized as oxides of N (Snyder et al. 2009).

Results of the study imply tclass="Chemical">hat the seasoclass="Chemical">nal split applicatioclass="Chemical">n of class="Chemical">n class="Species">cattle manure in small doses to wetland vegetable crops as a mitigation measure for reducing the emission of N2O from agricultural sources is effective during the first two seasonal split applications. Any further seasonal split applications of cattle manure in smaller doses to wetland vegetable crops cannot act as an effective crop management practice that reduces the emission of N2O from soil.

Effect of single and seasonal split application of manure on plant dry matter yield and soil N uptake

The class="Chemical">nitrogen use efficieclass="Chemical">ncy (class="Chemical">n class="Chemical">NUE) by the wetland vegetable crops could conceivably limit the loss of N from applied manure through gaseous emissions of N2O from soil. N is often cited as a limiting factor for vegetable growth in sub-tropical Africa. However, under conditions of elevated soil N, vegetable crops exhibit luxury consumption of N, leading to elevated tissue N concentration. While this pool of plant N may have benefits for vegetable plants if light levels change, it may also increase the risk of vegetable aboveground biomass quality (De Lannoy 2001). The differences between dry matter and uptake of N by the crops subjected to single basal applications and those receiving split applications of manure was smaller at the end of the experiment. This trend in the uptake of N by the crops is attributable to the initial abundance of N-rich easily decomposable organic compounds in the manure in plots that received single applications of cattle manure in four cropping events. Available forms of N became abundant in the wetland soil upon microbial decomposition of the nitrogenous compound pools, which increased root growth for the uptake of N.

The vegetable plots amended with split applications at every class="Gene">croppiclass="Chemical">ng eveclass="Chemical">nt class="Chemical">n class="Chemical">had initially insufficient N due to the limited quantities of manure added to create a larger net balance of mineralized N for uptake by the poorly developed root systems of the crops. The introduction of easily degradable C-rich materials in soil may have triggered a burst of microbial growth and activity that placed a burden on the limited quantities of mineralized N thereby depleting it significantly. Despite the comparatively narrow C:N ratio in the applied manure (Table 2, C:N ratio of 16.8:1), the quantities of N which was limited by the mass of manure applied in small doses may have been insufficient to introduce relatively large net balances of mineralized N after immobilization by microbes (Markewich et al. 2010), immobilization by reactive phenols from lignin degradation (Snyder et al. 2009; Kamaa et al. 2011), emissions by denitrification (Ma et al. 2007; Vasileiadou et al. 2011) and N loss by nitrate leaching (Johnson et al. 2005; Berdad-Haughn et al. 2006). The net result was a greater uptake of N in plots that received single basal applications of 15 and 30 Mg low N manure over that in vegetable plots that were subjected to split applications of 3.75 and 7.5 Mg low N manure observed in this study.

Increased dry matter accumulations on plots subjected to higher class="Species">cattle maclass="Chemical">nure applicatioclass="Chemical">ns was followed by higher uptake of class="Chemical">n class="Chemical">N from the applied fertilizers (Table 7). Consequently, plots that were amended with higher rates of manure applications effectively sequestered N that may be exposed to denitrification and the associated emissions of N2O. With improved accumulations of dry matter and N uptake in plots subjected to higher manure applications, the applied N in manure was effectively sequestered from the wetland soil where it may be subjected to loss through emissions of N2O. This implies that when agronomic practices are improved through manure applications, the loss of N in N2O emissions may significantly decrease.

Conclusions

Generally, it can be concluded tclass="Chemical">hat the seasoclass="Chemical">nal applicatioclass="Chemical">n of class="Chemical">n class="Species">cattle manure in small doses as a crop management mitigation measure for reducing the emissions of N2O from soil is effective at least up to the second seasonal split application. Thereafter, seasonal split applications of manure in smaller doses for every cropping event cannot reduce the losses of N from wetland soil in emissions of N2O. The improved uptake of N by the wetland vegetable crops can limit the loss of N from applied manure through gaseous emissions of N2O from soil.

Generally, the proportion of applied class="Chemical">N lost as class="Chemical">n class="Chemical">N2O was higher in the rape crop than in the tomato crop. It can be concluded that rape and possibly other similar leafy vegetables production has a greater potential to emit N2O into the atmosphere than the production of tomatoes in wetlands when cattle manure is used as a fertilizer. The loss of N in emissions of N2O expressed per unit mass of harvested dry matter yield of rape and tomato crops decreases significantly with increasing manure application rates, dry matter yield and N uptake. Improved agronomic practices for increased crop productivity can be used as a mitigation factor for reducing the contribution of agriculture in the global emissions of N2O.