About this Journal Submit a Manuscript Table of Contents
Applied and Environmental Soil Science
Volume 2012 (2012), Article ID 848612, 8 pages
http://dx.doi.org/10.1155/2012/848612
Research Article

Effect of ISPAD Anaerobic Digestion on Ammonia Volatilization from Soil Applied Swine Manure

1Department of Bioresource Engineering, Macdonald Campus, McGill University, 21111 Lakeshore, Ste. Anne de Bellevue, QC, Canada H9X 3V9
2Department of Natural Resource Sciences, McGill University, Macdonald Campus, 21111 Lakeshore, Ste. Anne de Bellevue, QC, Canada H9X 3V9
3Chaire de Recherche Internationale, Université Européenne de Bretagne, 35000 Rennes, France

Received 21 May 2011; Accepted 14 June 2011

Academic Editor: David C. Weindorf

Copyright © 2012 Susan King et al. This is an open access article distributed under the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.

Abstract

Swine manure subjected to in-storage psychrophilic anaerobic digestion (ISPAD) undergoes proteins degradation but limited NH3 volatilization, producing an effluent rich in plant-available nitrogen. Accordingly, ISPAD effluent can offer a higher fertilizer value during land application, as compared to manure of similar age stored in an open tank. However, this additional nitrogen can also be lost by volatilization during land application. The objective of this study was therefore to measure NH3 volatilization from both ISPAD and open tank swine manures when applied to 5 different soils, namely, washed sand, a Ste Rosalie clay, an Upland sandy loam, a St Bernard loam, and an Ormstown loam. This research was conducted using laboratory wind tunnels simulating land application. The five experimental soils offered similar pH values but different water holding capacity, cation exchange capacity, cation saturation, and organic matter. After 47 h of wind tunnel monitoring, the % of total available nitrogen (TAN or and NH3) volatilized varied with both manure and soil type. For all soil types, the ISPAD manure consistently lost less NH3 as compared to the open tank manure, averaging 53% less. Lower volatile solids content improving manure infiltration into the soil and a more complex ionic solution explain the effect of the ISPAD manure advantages. This was reinforced by the St Bernard sandy loam losing the same nitrogen mass for both manures, because of its higher pH and buffer pH coupled with an intermediate CEC resulting in more soil solution NH3. Within each manure type, % TAN volatilized was highest for washed sand and lowest for the clay soil. As a result, ISPAD manure can offer up to 21% more plant-available nitrogen fertilizer especially when the manure is not incorporated into the soil following its application.

1. Introduction

In-storage psychrophilic anaerobic digestion (ISPAD) occurs in manure storage tanks with an air-tight cover when its anaerobic microbial community acclimates to ambient conditions [1]. Developed for livestock operations in temperate climatic zones, ISPAD can release 65% of the manure’s potential methane while lowering volatile solids by 24% [1]. As opposed to mesophilic, psychrophilic anaerobic digestion limits biogas ammonia (NH3) levels, despite the breakdown of proteins [2, 3]. However, when land spread, the treated effluent may lose to the atmosphere the conserved total available nitrogen (TAN or and NH3), resulting in a net loss of nitrogen lowering its fertilizer value.

Following land spreading, the volatilization of NH3-N from swine manure depends on several factors. Some are independent of manure storage and treatment, such as pig diet [4], method of soil application [5], application timing [6], and subsequent weather conditions [79]. Diet manipulations reducing protein intake result in lower manure TAN and less volatilization losses following land application [10]. A data base analysis from field measurements concluded that NH3 volatilization was proportional to the manure TAN and the percentage released remained constant [7].

The concentration and thus volatilization of NH3 are also influenced by the manure characteristics and their interaction with the soil properties. The speciation of TAN into NH3 depends not only on the pH and temperature of the manure [11, 12] but also on the presence of other ionized species [13]. The soil alkalinity and buffering capacity can change the manure pH [11, 14, 15]. The NH3 speciation equilibrium is further affected by the soil cation exchange capacity (CEC) affecting the level of free [16]. Furthermore, can be precipitated by soil solution cations, particularly Ca2+ and Mg2+, producing calcite and struvite [12].

Physical aspects of the soil/manure system also intervene. Lower NH3 volatilization results from higher manure infiltration into the soil, especially when the manure has a low volatile solids content [8]. Nevertheless, manure applied on a dry soil loses its water content releasing NH3 [17].

Anaerobic digestion can change the physicochemical characteristics of swine manure thereby influencing several of the above-mentioned factors. Untreated and anaerobically digested under mesophilic conditions, swine manure offered the same rate of NH3 volatilization after application to grassland [18]. In a similar comparison, soil pH and -N content were found to be more influential following the application of both treated and untreated swine manures to bare soil [19]. In comparison to untreated manure, NH3 volatilization was 22% less for anaerobically digested manure applied to a bare silty clay loam [20].

While similar nutrient values (N, P, and K) are found for swine manures from all types of operations and in several countries [2123], plant availability depends on best management practices [24]. Anaerobic digestion degrades organic N releasing TAN [2, 25, 26] readily available for plant uptake. Once soil applied and as compared to untreated manure, digested effluents were found to offer higher plant available nutrients for wheat [27], corn [28], and timothy [29].

Accordingly, ISPAD can enhance the manure N fertilizer value by minimizing biogas NH3 content as compared to mesophilic systems, while still providing all benefits of anaerobic digestion and higher plant-available N. The objective of the present study was therefore to compare the extent of NH3 volatilization between ISPAD treated and raw (untreated or open tank) swine manures. This was done by simulating land application of both manures using the wind tunnel technique and monitoring NH3 release with boric acid traps. Five different experimental soils were used, each offering a similar pH but different cation exchange capacity (CEC), cation saturation level, organic matter content, and water holding capacity.

2. Materials and Methods

2.1. Experimental Manures and Soils

In 2004, a full-scale swine manure ISPAD was established in St. Francois Xavier, Quebec, Canada, using a circular concrete tank, 30 m in diameter and 3.66 m deep, covered with an air-tight membrane (GTI, Fredericton, NB, Canada). The ISPAD was fed swine manure weekly and was emptied in the spring and fall of each year, except for a 0.3–0.6 m depth. In 2010 for the present experiment, manure from this facility was compared to 12-month-old swine manure from the open tank of the Experimental Swine Facility of McGill University at its Macdonald Campus, Montreal, Canada. Produced by hogs fed a standard corn and soybean ration, these two manures were considered comparable in terms of solids and nutrients [21]. All manure samples were collected in March 2010 using a sludge-judge apparatus to obtain a composite sample representing the average of depths and locations within the tanks [1].

Manure samples were analyzed according to standard methods [30] for solids, pH, total Kjeldahl nitrogen (TKN), total ammonia nitrogen (TAN), and phosphorus (P) and potassium (K) content. Total solids (TSs) were determined by drying whole samples at 103°C overnight (VWR, Sheldon Manufacturing, model 1327F, OR, USA). Volatile solids (VS) were determined by incineration of dried samples at 500°C for two hours (Barnstead Thermodyne, model 48000, Iowa, USA). Fixed solids (FSs) were computed as the difference between VSs from TS. The pH of all samples was determined using a pH meter (Corning, model 450, NY, USA). The TKN, P, and K were determined by digesting samples of each manure with sulphuric acid and 50% hydrogen peroxide at 500°C for 15 minutes (Hach Canada, Digesdahl model 23130-20, Mississauga, ON). Subsamples of digestate were used to quantify P and K colorimetrically at a pH of 7, using a spectrophotometer (Hach, model DR 5000, Loveland Clo, USA). For TKN, the pH of subsamples was adjusted to 13 using NaOH, and the NH3-N content was measured with an NH3-sensitive electrode (Orion, Boston Mass, USA) connected to a pH meter (Corning, model 450, NY, USA). Total ammonia nitrogen was measured in the same way using undigested samples, after adjusting the pH to 13.

The five experimental soils were washed sand (S. Boudrias Inc., Laval, QC, Canada), Ste Rosalie clay from Howick, Canada, 50 km west of Montreal; Upland sandy loam from Ste Anne de Bellevue, Canada at the western tip of the Montreal Island, St Bernard loam also from Ste Anne de Bellevue at the western tip of the Montreal Island, and Ormstown loam from Ormstown, Canada, 70 km west of Montreal. Except for the washed sand, all soils were collected from the ground surface for a minimum organic matter content of 3.9%. All soils were dried and ground before sieving to remove organic particles larger than 6 mm.

All experimental soils were analyzed using standard methods. After soaking for 24 hours in equal amounts of distilled water, pH was determined using a pH electrode [31]. Organic matter content was determined on samples dried at 150°C for 16 hours, using a muffle furnace at 375°C for 16 hours [32]. Minerals and trace elements were measured first by extracting with a Mehlich III solution and then by plasma emission spectrometry [33]. The CEC was determined by saturating the samples with using an ammonium acetate solution at pH 7 and then quantifying the released after adding an NaCl solution [34]. Total Kjeldahl nitrogen was measured after sulphuric acid/peroxide digestion using an NH3-sensitive probe connected to a pH meter (Orion, Boston, USA). Soil particle size distribution was determined using the hydrometer method [35]. The gravimetric water holding capacity was measured by soaking previously dried subsamples in distilled water for 24 hours and draining under cover to prevent evaporation.

2.2. Experimental Wind Tunnels

Ammonia volatilization tests were conducted using five wind tunnels designed for manure spreading simulations [36]. Measuring 2.0 m in length, with an inlet diffuser and outlet reducer of 0.3 and 0.15 m, respectively, each tunnel sat on a soil pan measuring 1.5 m long × 0.1 m wide × 0.05 m deep (Figure 1). Connected in parallel, each wind tunnel received the same fresh air at a rate maintaining a consistent inside air speed of 0.3 ms−1. Exhaust air from each wind tunnel was routed through 3 mm Teflon tubing (Laurentian Valve & Fittings ltd., Saint-Laurent, Canada) into NH3 traps consisting of 250 mL of 0.32 M HBO3 indicator solution in a sealed 500 mL flask [37], at a rate of 6 L min−1 using a 0.5 kW vacuum pump (Gast, model 0823, Wainbee ltd., Pointe-Claire, QC, Canada). Flow meters (Rate-Master, model RMA-21-BV, ITM, Ste-Anne-de-Bellevue, QC, Canada) adjusted the air flow of each wind tunnel line.

848612.fig.001
Figure 1: Wind tunnels used for the laboratory manure land application simulations to measure NH3 volatilization. The wind tunnel is set on a spreading pan holding 50 mm of experimental soil. Fresh air is introduced through the bottom left hand pipe, circulated through the body at a speed of 3 m s−1 and exited through the top right hand pipe. To measure NH3 volatilization, a known portion of the outlet air was bubbled through an acid solution.
2.3. Land Application Simulation

Land application simulations for the ISPAD and the open tank swine manures were tested in triplicates on all five soil types, resulting in 30 simulations. For each simulation using all five wind tunnels, 7.5 L of prepared soil was spread in each soil pan and water was added to bring its water content to 25% of its gravimetric holding capacity. Manure samples were weighed and then quickly but uniformly applied to the soils by hand at a simulated rate of 115 kg TKN ha−1. The tunnels were quickly placed on the pans and airflow was started immediately.

Volatilized NH3 was measured after 2, 4, 6, 8, 24 and 47 hours, by replacing the acid trap with a fresh one. The removed acid traps were chilled to 4°C before analysis for -N by titration with 0.1 M HCl [37]. Ammonia volatilization was computed from the air flow ratio of the acid trap and wind tunnel, at a constant ambient air temperature of 21°C.

2.4. Statistical Analysis

All statistical analyses were performed using SAS 9.2 (2010, SAS Institute inc., Cary NC, USA). The triplicate manure and soil characterization was used to determine the significance between measured values using the Student-Newman-Keuls method in a simple analysis of variance based on a completely randomized design. The NH3 volatilization wind tunnel tests used a randomized complete block design, considering manure type as the treatment factor and soil type as the block factor. The dependant variable was NH3 volatilization. Treatments were assigned randomly to experimental units (wind tunnels) and all treatments-block combinations were completed in triplicate.

3. Results and Discussion

3.1. Experimental Manure and Soil Characteristics

The experimental manures are characterized in Table 1. Despite similar contents, the VS : TS and VS : FS ratios were significantly different (), reflecting the lower organic matter content of the ISPAD manure as a result of anaerobic digestion. Considering that suspended solids are volatile solids by nature and that both manure had similar level of dissolved solids, it can therefore be concluded that the ISPAD manure had less suspended solids as compared to that from the open tank.

tab1
Table 1: Characteristics of experimental manures where both the ISPAD or anaerobically digested manure and the open tank or untreated manure are one year old.

Both the ISPAD and open tank manures offered a similar pH and TKN, but their VS : TS and TAN : TKN ratios were significantly different ( and 0.0407, resp.) at 0.69 and 0.49, respectively, indicating greater protein breakdown for the ISPAD manure [2]. The total P and K contents were similar. The ISPAD manure demonstrated some loss of NH3 during sampling and transportation, based on its TKN : FS ratio compared to that of the open tank manure.

This combination of similarities and differences provided a wind tunnel comparison based on the significantly different characteristics of the two manures for the 115 kg TKN ha−1 applied. The similar TKN resulted in the same volume of manure being applied, thus conserving similar soil water holding capacity levels. Similar TS but different VS levels were applied. The TAN was the most important difference between manures, which was reported not to affect % N volatilization [7, 19]. Accordingly, the application of ISPAD and open swine manures provided a TAN level of 79 and 56 kg ha−1.

The experimental soils (Table 2) were selected to offer a range of properties, illustrated by the groupings produced by the Student-Newman-Keuls test. Organic matter was similar only between the St Bernard loam and Ste Rosalie clay; gravitational water holding capacity was similar for the Upland sandy loam, St Bernard loam, and Ormstown loam; CEC, particle size distribution, especially clay content, and TKN differed among all soils. The pH was similar between the St Bernard loam and Ste Rosalie clay at 6.9 and 6.8, respectively, but different for the rest of the soils offering a pH of 6.3 to 6.5. The mass balance attempted between the initial soil and final soil manure TKN levels were inconclusive because the applied manure TKN was much smaller.

tab2
Table 2: Characteristics of the five experimental soils used to measure NH3 volatilization for the two experimental manures, untreated (open tank) and anaerobically treated (ISPAD).
3.2. Ammonia Volatilization

The NH3 volatilized from all five soils and the two experimental swine manures are compared in Figures 2(a) and 2(b). After 47 hours, the ISPAD swine manure had lost significantly less TAN, from 8 to 37% of that applied, while the open tank manure had lost from 25 to 61%. Accordingly, the ISPAD manure suffered from 75 to 50% less TAN losses as compared to the open tank manure, depending on the soil type. Considering that the two experimental manures offered similar properties except for their treatment, reflecting VS : TS and TAN : TKN ratio, anaerobic digestion was found to reduce NH3 volatilization. Similar results were obtained in a field experiment using different crops grown on a loamy soil in Germany [38]. As compared to untreated manure, anaerobically digested manure lost volatilized NH3 equivalent to 14.2 as opposed to 13% of its total N applied, which represents 20 as opposed to 26% of its TAN.

fig2
Figure 2: Cumulative NH3 volatilized during 47 hours following the land application of untreated swine manure from the open tank (a) and anaerobically treated swine manure ISPAD (b). The NH3 volatilization was measured using the laboratory wind tunnels. The data points are the average of and the error bars represent ± one standard deviation.

The ISPAD manure not only suffered significantly less NH3 volatilization losses over 47 hours but also exhibited a rate of loss which leveled off at 47 hours as opposed to that of the open tank manure. After 47 hours, the ISPAD manure was losing TAN at a rate of 0.25 to 0.05% h−1 for all five experimental soils, as compared to the open tank manure loosing TAN at a rate of 1.7 to 0.25% h−1.

The statistical analysis using both mg NH3-N and % TAN volatilized revealed that the effect of both manure and soil types was significant ( for mg N and for % TAN), with no significant interaction between the factors in either case. The significance of manure effect in mg N confirms that the results were not limited by air saturation in NH3 inside the wind tunnels, which would have resulted in equal values among tunnels despite higher % TAN losses. Therefore, the remaining results will be presented in terms of % TAN volatilized.

Past research demonstrated a consistent % TAN volatilized for different application rates, with other factors held constant. For the present study, the significant effect results from the manure treatment as both manures exhibited similar properties. For anaerobically digested manure, the specific properties reducing NH3 volatilization are lower volatile solids allowing for an improved infiltration into the soil and more complex ionic solution lowering TAN speciation into NH3 [8, 13].

Comparing soil type, the % TAN volatilized results were grouped using the Student-Newman-Keuls method, indicating that, for each manure type, volatilizations from the Upland sandy loam, St Bernard loam, and Ormstown loam soil series were statistically similar while those from the Ste Rosalie clay and the washed sand were each significantly different. For each manure type, volatilization was highest for the washed sand, intermediate for the three similar soils, and lowest for the Ste Rosalie clay, the same grouping observed for H2O holding capacity and CEC.

Exploratory plots of % TAN volatilized versus each individual soil property also revealed patterns suggesting linear relationships for water holding capacity, CEC and cation saturation. These relationships were examined using a two-factorial rather than a blocked experimental design, which compared the qualitative rather than quantitative soil type values. A variety of combinations revealed a significant effect of the water holding capacity and CEC (), but only when considered separately. The use of only two manure types limited the scope of analysis available, but interesting leads for future research suggest extracting a numerical equation relating the appropriate manure and soil characteristics to % TAN volatilized.

Table 3 summarizes the % and mass (kg ha−1) TAN volatilized in 47 h for each manure-soil combination. The ISPAD manure was found to lose 46% less TAN than the open tank manure. The washed sand lost the most % TAN while the Ste Rosalie clay lost the least at 33% less than the washed sand. The 3 intermediate soils lost approximately 54% of the TAN compared to the washed sand. Interestingly enough, the St Bernard loam lost the same mass of NH3-N for both manure types, likely because of its higher pH and buffer as compared to the other soils and average CEC, resulting in more soil solution NH3. Accordingly, the ISPAD manure benefited from the combined effect of its lower volatile solids (VSs) and a more complex ionic solution lowering TAN speciation into NH3 resulting in lower volatilization for higher levels of plant-available nitrogen [39].

tab3
Table 3: Fraction of the manure TAN volatilized in 47 hours of wind tunnel simulations for the five experimental soils and two manures, untreated (open tank) and anaerobically digested (ISPAD).
3.3. ISPAD Manure N Fertilizer Value

Because of stringent requirements for nutrient management planning all over North America, the Quebec Ministry of Environment has produced detailed methods for calculating the fertilizer value of manures [34, 40]: where CEFO is the organic fraction efficiency factor based on C : N ratio, CV is the volatilization factor based on land application method, CA is the availability factor based on application date (spring or fall), and CP is the previous application factor based on years of manure applied.

Using (1), was calculated for the two experimental manures, assuming three possible cases selected to illustrate a full range of situations: Case  1 pertained to an immediate incorporation of the manure into a clay soil supporting row crops, in the spring; Case  2 pertained to the incorporation within 48 hours of the manure into a sandy loam soil in row crops, during the early summer; Case  3 pertained to manure left at the surface of a sandy loam soil supporting a hayfield, in the autumn. In all cases and for simplicity, no manure was presumed previously applied to the fields, thus CP = 1. For both manures, a C : N ratio in the range of 6 to 10 : 1 was assumed, based on the VS and TKN values (Table 1). The CV value for the ISPAD manure was modified using the ratio of 0.53 obtained by comparing NH3 volatilized between the ISPAD and open tank manures in Table 3:

The resulting N fertilizer values summarized in Table 4 demonstrate that in Case  1, representing the ideal manure land-application conditions, the ISPAD manure has a modest advantage of 6% over the open tank manure. This advantage increases to 18% under Case  2 where manure is spread on land and then incorporated within 48 hours. For Case  3, where no soil incorporation is practiced, the ISPAD manure offers the highest advantage of 21%. Accordingly, for the same P content, ISPAD manure can provide up to 21% more plant-available N than open tank manure, thus reducing the mineral nitrogen required for top-up by an equivalent amount.

tab4
Table 4: Manure N fertilizer value for similar P and K applications for the two experimental manures, untreated (open tank) and anaerobically digested (ISPAD).

4. Conclusions

The objective of this study was to compare the NH3 volatilization potential of swine manure treated by a five-year-old in-storage psychrophilic anaerobic digestion system (ISPAD) against that from an open tank. The study simulated field spreading in the laboratory using wind tunnels and five soils offering a different texture and chemical properties.

The study revealed the following. (i)For all experimental soils, the % TAN volatilized from the ISPAD manure was on the average 46% lower than that from an open tank indicating the beneficial effect of anaerobic digestion, such as lowering the volatile solids reflecting the suspended solids concentration, to improve infiltration and producing a more complex ionic solution lowering TAN speciation into NH3. (ii)Water holding capacity and cation exchange capacity were the most important soil parameters influencing NH3 volatilization. (iii)The ISPAD and open tank manures offered a TAN : TKN ratio of 69 and 49%, respectively; coupled with a lower NH3 volatilization, ISPAD manure can thus increase by up to 21% the plant-available N for the same P andK value, as compared to open tank manure.

Further research is required to identify more clearly the parameters of ISPAD manure which facilitate its lower NH3 volatilization during land spreading.

Acknowledgments

The authors wish to acknowledge the financial contributions of the Natural Science and Engineering Research Council of Canada, Geomembrane Technologies Inc., of Fredericton NB, Canada, and the Coop Fédérée (Montréal, Canada), the technical contribution of Consumaj Inc., of Ste-Hyacinthe, QC, Canada, and the personal contributions of Dr. Alice Cherestes.

References

  1. S. M. King, S. Barrington, and S. R. Guiot, “In-storage psychrophilic anaerobic digestion: acclimation of the microbial community,” submitted to Biomass and Bioenergy. View at Publisher · View at Google Scholar
  2. S. M. King, S. Barrington, and S. R. Guiot, “In-storage psychrophilic-anaerobic-digestion of swine manure: protein degradation and interactions,” submitted to Biomass and Bioenergy. View at Publisher · View at Google Scholar
  3. D. P. B. T. B. Strik, A. M. Domnanovich, and P. Holubar, “A pH-based control of ammonia in biogas during anaerobic digestion of artificial pig manure and maize silage,” Process Biochemistry, vol. 41, no. 6, pp. 1235–1238, 2006. View at Publisher · View at Google Scholar · View at Scopus
  4. J. S. Paschold, B. J. Wienhold, D. L. McCallister, and R. B. Ferguson, “Crop nitrogen and phosphorus utilization following application of slurry from swine fed traditional or low phytate corn diets,” Agronomy Journal, vol. 100, no. 4, pp. 997–1004, 2008. View at Publisher · View at Google Scholar · View at Scopus
  5. P. Rochette, M. H. Chantigny, D. A. Angers, N. Bertrand, and D. Côté, “Ammonia volatilization and soil nitrogen dynamics following fall application of pig slurry on canola crop residues,” Canadian Journal of Soil Science, vol. 81, no. 4, pp. 515–523, 2001. View at Scopus
  6. R. Gordon, R. Jamieson, V. Rodd, G. Patterson, and T. Harz, “Effects of surface manure application timing on ammonia volatilization,” Canadian Journal of Soil Science, vol. 81, no. 4, pp. 525–533, 2001. View at Scopus
  7. J. F. M. Huijsmans, J. M. G. Hol, and G. D. Vermeulen, “Effect of application method, manure characteristics, weather and field conditions on ammonia volatilization from manure applied to arable land,” Atmospheric Environment, vol. 37, no. 26, pp. 3669–3680, 2003. View at Publisher · View at Google Scholar · View at Scopus
  8. T. H. Misselbrook, F. A. Nicholson, and B. J. Chambers, “Predicting ammonia losses following the application of livestock manure to land,” Bioresource Technology, vol. 96, no. 2, pp. 159–168, 2005. View at Publisher · View at Google Scholar · View at Scopus
  9. M. S. Mkhabela, R. Gordon, D. Burton, E. Smith, and A. Madani, “The impact of management practices and meteorological conditions on ammonia and nitrous oxide emissions following application of hog slurry to forage grass in Nova Scotia,” Agriculture, Ecosystems & Environment, vol. 130, no. 1-2, pp. 41–49, 2009. View at Publisher · View at Google Scholar · View at Scopus
  10. G. L. Velthof, J. A. Nelemans, O. Oenema, and P. J. Kuikman, “Gaseous nitrogen and carbon losses from pig manure derived from different diets,” Journal of Environmental Quality, vol. 34, no. 2, pp. 698–706, 2005. View at Scopus
  11. Y. Avnimelech and M. Laher, “Ammonia volatilization from soils: equilibrium considerations,” Soil Science Society of America Journal, vol. 41, no. 6, pp. 1080–1084, 1977. View at Scopus
  12. S. G. Sommer, S. Génermont, P. Cellier, N. J. Hutchings, J. E. Olesen, and T. Morvan, “Processes controlling ammonia emission from livestock slurry in the field,” European Journal of Agronomy, vol. 19, no. 4, pp. 465–486, 2003. View at Publisher · View at Google Scholar · View at Scopus
  13. S. D. Hafner and J. J. Bisogni, “Modeling of ammonia speciation in anaerobic digesters,” Water Research, vol. 43, no. 17, pp. 4105–4114, 2009. View at Publisher · View at Google Scholar · View at Scopus
  14. S. Husted, L. S. Jensen, and S. S. Jorgensen, “Reducing ammonia loss from cattle slurry by the use of acidifying additives: the role of the buffer system,” Journal of the Science of Food and Agriculture, vol. 57, pp. 335–349, 1991.
  15. P. L. G. Vlek and J. M. Stumpe, “Effects of solution chemistry and environmental conditions on ammonia volatilization losses from aqueous systems,” Soil Science Society of America Journal, vol. 42, no. 3, pp. 416–421, 1978.
  16. P. O'Toole, S. J. McGarry, and M. A. Morgan, “Ammonia volatilization from urea-treated pasture and tillage soils: effects of soil properties,” European Journal of Soil Science, vol. 36, pp. 613–620, 1985.
  17. S. G. Sommer, L. S. Jensen, S. B. Clausen, and H. T. Søgaard, “Ammonia volatilization from surface-applied livestock slurry as affected by slurry composition and slurry infiltration depth,” Journal of Agricultural Science, vol. 144, no. 3, pp. 229–235, 2006. View at Publisher · View at Google Scholar · View at Scopus
  18. B. F. Pain, T. H. Misselbrook, C. R. Clarkson, and Y. J. Rees, “Odour and ammonia emissions following the spreading of anaerobically-digested pig slurry on grassland,” Biological Wastes, vol. 34, no. 3, pp. 259–267, 1990. View at Publisher · View at Google Scholar · View at Scopus
  19. M. H. Chantigny, P. Rochette, D. A. Angers, D. Massé, and D. Côté, “Ammonia volatilization and selected soil characteristics following application of anaerobically digested pig slurry,” Soil Science Society of America Journal, vol. 68, no. 1, pp. 306–312, 2004. View at Scopus
  20. M. H. Chantigny, J. D. MacDonald, C. Beaupré et al., “Ammonia volatilization following surface application of raw and treated liquid swine manure,” Nutrient Cycling in Agroecosystems, vol. 85, no. 3, pp. 275–286, 2009. View at Publisher · View at Google Scholar · View at Scopus
  21. K. L. Conn, E. Topp, and G. Lazarovits, “Factors influencing the concentration of volatile fatty acids, ammonia, and other nutrients in stored liquid pig manure,” Journal of Environmental Quality, vol. 36, no. 2, pp. 440–447, 2007. View at Publisher · View at Google Scholar · View at Scopus
  22. A. D. Moore, D. W. Israel, and R. L. Mikkelsen, “Nitrogen availability of anaerobic swine lagoon sludge: sludge source effects,” Bioresource Technology, vol. 96, no. 3, pp. 323–329, 2005. View at Publisher · View at Google Scholar · View at Scopus
  23. M. Sánchez and J. L. González, “The fertilizer value of pig slurry. I. Values depending on the type of operation,” Bioresource Technology, vol. 96, no. 10, pp. 1117–1123, 2005. View at Publisher · View at Google Scholar · View at Scopus
  24. J. Schröder, “Revisiting the agronomic benefits of manure: a correct assessment and exploitation of its fertilizer value spares the environment,” Bioresource Technology, vol. 96, no. 2, pp. 253–261, 2005. View at Publisher · View at Google Scholar · View at Scopus
  25. J. A. Field, J. S. Caldwell, S. Jeyanayagam, R. B. Reneau, W. Kroontje, and E. R. Collins, “Fertilizer recovery from anaerobic digesters,” Transactions of the American Society of Agricultural Engineers, vol. 27, no. 6, pp. 1871–1881, 1984. View at Scopus
  26. C. E. Marcato, R. Mohtar, J. C. Revel, P. Pouech, M. Hafidi, and M. Guiresse, “Impact of anaerobic digestion on organic matter quality in pig slurry,” International Biodeterioration and Biodegradation, vol. 63, no. 3, pp. 260–266, 2009. View at Publisher · View at Google Scholar · View at Scopus
  27. S. P. Dahlberg, J. A. Lindley, and J. F. Giles, “Effect of anaerobic digestion of nutrient availability from dairy manure,” Transactions of the American Society of Agricultural Engineers, vol. 31, no. 4, pp. 1211–1216, 1988. View at Scopus
  28. E. R. Loria, J. E. Sawyer, D. W. Barker, J. P. Lundvall, and J. C. Lorimor, “Use of anaerobically digested swine manure as a nitrogen source in corn production,” Agronomy Journal, vol. 99, no. 4, pp. 1119–1129, 2007. View at Publisher · View at Google Scholar · View at Scopus
  29. M. H. Chantigny, D. A. Angers, P. Rochette, G. Bélanger, D. Massé, and D. Côté, “Gaseous nitrogen emissions and forage nitrogen uptake on soils fertilized with raw and treated swine manure,” Journal of Environmental Quality, vol. 36, no. 6, pp. 1864–1872, 2007. View at Publisher · View at Google Scholar · View at Scopus
  30. APHA, AWWA, WEF, Standard Methods for Examination of Water and Wastewater, American Public Health Association, Washington, DC, USA, 2005.
  31. CEAE, Determination du pH a l'Eau dans les Sols Agricoles, Centre d'expertise en analyse environnemental du Québec. Ministere de l'Agriculture, de l'Alimentation et des Pêcheries du Québec, Ministere du Développement durable, de l'Environnement du Québec, Quebec, Canada, 2003.
  32. CEAE, Determination de la Matiere Organique par Incineration: Methode de Perte de Feu (PAF), Centre d'expertise en analyse environnemental du Québec. Ministere de l'Agriculture, de l'Alimentation et des Pêcheries du Québec, Ministere du Développement durable, de l'Environnement du Québec, Quebec, Canada, 2003.
  33. CEAE, Determination des Metaux Extractables dans les Sols Agricoles: Methode par Spectrometrie d'Emission au Plasma d'Argon ou par Spectrometrie d'Absorption Atomique apres Extraction avec la Methode Mehlich III, Centre d'expertise en analyse environnemental du Québec. Ministere de l'Agriculture, de l'Alimentation et des Pêcheries du Québec, Ministere du Développement durable, de l'Environnement du Québec, Quebec, Canada, 2003.
  34. CRAAQ, Guide de Reference en Fertilisation, Centre de Reference en Agriculture et Agroalimentaire du Quebec, Quebec, Canada, 1st edition, 2003.
  35. B. H. Sheldrick and C. Wang, “Particle size distribution,” in Soil Sampling and Methods of Analysis, M. R. Carter, Ed., pp. 499–511, Lewis Publishers, Boca Raton, Fla, USA, 1993.
  36. D. Choinière, S. Barrington, and C. Foulds, “A validated evaluation protocol for odour reducing additives during swine manure spreading,” in International Symposium on air Quality and Waste Management for Agriculture, Broomfield, Colo, USA, 2007, ASABE publication number 701P0907cd.
  37. D. M. Miles, P. R. Owens, P. A. Moore, and D. E. Rowe, “Instrumentation for evaluating differences in ammonia volatilization from broiler litter and cake,” Journal of Applied Poultry Research, vol. 17, no. 3, pp. 340–347, 2008. View at Publisher · View at Google Scholar · View at Scopus
  38. K. Möller and W. Stinner, “Effects of different manuring systems with and without biogas digestion on soil mineral nitrogen content and on gaseous nitrogen losses (ammonia, nitrous oxides),” European Journal of Agronomy, vol. 30, no. 1, pp. 1–16, 2009. View at Publisher · View at Google Scholar · View at Scopus
  39. R. Gutser, T. Ebertseder, A. Weber, M. Schraml, and U. Schmidhalter, “Short-term and residual availability of nitrogen after long-term application of organic fertilizers on arable land,” Journal of Plant Nutrition and Soil Science, vol. 168, no. 4, pp. 439–446, 2005. View at Publisher · View at Google Scholar · View at Scopus
  40. MDDEP, Reglement sur les Exploitations Agricoles c. Q-2,r.11-1, Editeur officiel du Quebec, Quebec, Canada, 2005.