Biosolids Soil Application: Agronomic and Environmental Implications 2014View this Special Issue
Research Article | Open Access
Virginia L. Jin, Kenneth N. Potter, Mari-Vaughn V. Johnson, R. Daren Harmel, Jeffrey G. Arnold, "Surface-Applied Biosolids Enhance Soil Organic Carbon and Nitrogen Stocks but Have Contrasting Effects on Soil Physical Quality", Applied and Environmental Soil Science, vol. 2015, Article ID 715916, 10 pages, 2015. https://doi.org/10.1155/2015/715916
Surface-Applied Biosolids Enhance Soil Organic Carbon and Nitrogen Stocks but Have Contrasting Effects on Soil Physical Quality
Mid- to long-term impacts of land applying biosolids will depend on application rate, duration, and method; biosolids composition; and site-specific characteristics (e.g., climate, soils). This study evaluates the effects of surface-broadcast biosolids application rate and duration on soil organic carbon (SOC) stocks, soil aggregate stability, and selected soil hydraulic properties in a municipally operated, no-till forage production system. Total SOC stocks (0–45 cm soil) increased nonlinearly with application rate in perennial grass fields treated for 8 years with 0, 20, 40, or 60 Mg of Class B biosolids (DM) ha−1 yr−1 (midterm treatments). Soil organic C stocks in long-term treatment fields receiving 20 years of 20 Mg ha−1 yr−1 were 36% higher than those in midterm fields treated at the same rate. Surface-applying biosolids had contrasting effects on soil physical properties. Soil bulk density was little affected by biosolids applications, but applications were associated with decreased water-stable soil aggregates, increased soil water retention, and increased available water-holding capacity. This study contrasts the potential for C storage in soils treated with surface-applied biosolids with application effects on soil physical properties, underscoring the importance of site-specific management decisions for the beneficial reuse of biosolids in agricultural settings.
Beneficial use of biosolids is a key management tool for publicly owned treatment works (POTWs) for waste utilization and is more highly regulated than land application of animal wastes [1–3]. When applied in compliance with regulations limiting trace metals inputs and at agronomically appropriate rates, land-applied biosolids are effective soil conditioners and can supplement or replace commercial inorganic fertilizers while improving soil water conservation . In addition to using biosolids amendments to restore or build soil quality, organic waste applications could promote the mitigation of atmospheric carbon dioxide levels by enhancing soil organic carbon (SOC) storage [5–7].
The quantity and frequency of inputs, method and timing of application, biosolids composition, and site edaphic factors (e.g., soils, climate) as well as other associated management practices (e.g., tillage, irrigation) affect the transfer of biosolids-C into SOC pools [7–12]. Several literature reviews show that inputs of biosolids-derived organic matter can lead to both short-term and longer-term increases in SOC [4, 7–9, 13]. Further, organic matter increases associated with land applying biosolids are often linked to improvements in soil physical quality, including decreased soil bulk density, increased soil aggregate stability, enhanced soil moisture retention, and lower soil erosion potential [5, 9–11, 14].
Soil responses to land application in no-till systems using surface-applied biosolids may differ from soil responses in cultivated management systems that use tillage to incorporate biosolids into surface soils. The available literature on surface-applied biosolids, particularly under field conditions, is limited relative to the number of published studies on incorporated biosolids. The objectives of this study were to evaluate the effect of application rate and duration on SOC stocks, soil aggregate stability, and selected soil hydraulic properties at a municipal biosolids recycling facility that surface-applies Class B biosolids on large-scale, no-till perennial forage production fields. Because the impact of biosolids applications on SOC and soil physical properties can be highly variable both temporally and spatially [11, 15, 16], studies assessing the mid- and long-term effects of repeated biosolids applications, such as the one conducted here, are critical to evaluate treatment effects and system sustainability in large-scale operational settings .
2. Materials and Methods
2.1. Site and Biosolids Descriptions
This site is a publicly owned, municipally operated 485 ha, zero-discharge facility in Travis County, Texas, USA. Soils are silt loams and silty clay loams (fine-silty, mixed, superactive, thermic Cumulic Haplustolls) and are very deep (>2 m to groundwater) and well drained, with slopes <1% . Study site and management descriptions were reported previously  and were recently updated .
Biosolids are land-applied as anaerobically digested, dewatered Class B biosolids. Biosolids originate from sewage solids pumped to this recycling center from two major municipal wastewater treatment facilities servicing almost 95% of the city population (~900,000). Solids are separated from the wastewater and thickened using a cationic, petroleum-based dewatering polymer before and after anaerobic digestion. Thickened digested biosolids are belt-pressed to further reduce water content and then stockpiled on-site until land application. Biosolids are analyzed monthly by the POTW, which provided values for selected biosolids properties for 12 consecutive months (ranges and means from , Table 1). Total organic C was measured in grab-samples of stockpiled biosolids (described in the next subsection). Regulated metal loadings were well below the 40 CFR Part 503 ceiling limits (data not shown) .
|Annual applications in this treatment reduced to biennial applications of 5 Mg ha−1 yr−1 in 2007.|
‡Environmental Protection Agency (EPA) or Standard Methods (SM) protocols used to quantify each constituent, in order listed: SW846 9060A; EPA 351.2; SM 4500-P BE; EPA 6020; SM 4500-H; EPA 9045D; SM 2540G.
All biosolids applications were managed by the municipal recycling facility and integrated with other facility operations. Biosolids were surface-applied with manure spreaders to ~220 ha of no-till perennial forage production fields of coastal bermudagrass (Cynodon dactylon L.), which included long-term (20 yr) and midterm (8 yr) application fields. All rates are reported in unit dry mass (DM). Forage was mechanically harvested multiple times per season, depending on productivity, and no grazing was used at this site. The long-term application field (14 ha) received 20 Mg biosolids ha−1 yr−1 from 1985 to 2005. Application rates were reduced to 5 Mg ha−1 yr−1 every 2 years in 2007 to comply with the facility’s nutrient management plan. A single application at this lower rate occurred before soil sampling in July 2009 (see next section). Midterm application fields were established in 2002 and consisted of 20 ha, 36 ha, and 49 ha parcels that received 20, 40, and 60 Mg ha−1 yr−1, respectively. Each parcel was split into two fields receiving the same application rate. Under municipal operating protocols, biosolids were applied one field at a time. Depending on field size, experimental application rate, the rate of sludge inputs from the municipality, and other operational constraints, biosolids were applied continuously to a given field until the target experimental annual treatment rate was fully applied (e.g., as short as 2-3 weeks or as long as 6–8 weeks). Surface applications would then proceed to the next field until all fields had been applied for the year. Biosolids were then stockpiled until the following year when surface applications could be resumed. Adjacent to the midterm 20 Mg ha−1 yr−1 area, a 2 ha coastal bermudagrass control field has no recorded history of any nutrient inputs from biosolids, animal or green manures, or commercial fertilizer.
2.2. Soil Sampling and Analyses
Soil cores (6.35 cm diameter, ~50 cm deep) were collected in July 2009 from treated fields (unamended control; 20 dry Mg biosolids ha−1 yr−1 for 20 yr; 20, 40, and 60 Mg ha−1 yr−1 for 8 yr) using a truck-mounted hydraulic soil probe. Soils were collected in fields that were not undergoing active application and where biosolids had not been applied for at least 30 days before sampling to comply with POTW safety requirements and EPA 40 CFR Part 503 reentry guidelines , respectively. Compliance with municipal operational guidelines and federal safety guidelines resulted in sampling soils from only one field per treatment level. Paired soil cores were collected at four or five locations at 50 m intervals along a transect that spanned the center of each treatment field. No cores were sampled within 50 m of the field edge due to possible edge effects (i.e., increased soil compaction due to higher equipment traffic). Visible biosolids and plant material were removed from the soil surface prior to sampling. Each core was collected in a clear polyethylene tube liner, transported to the laboratory, and then extruded and separated into the following depth increments: 0–5, 5–10, 10–15, 15–25, 25–35, and 35–45 cm. Selected soil properties from July 2009 are presented for 0–30 cm soils collected separately from those used in this study (Table 2).
|Annual applications in this treatment reduced to biennial applications of 5 Mg ha−1 yr−1 in 2007. bParticle size distributions (sand, silt, and clay) were determined by hydrometer ; pH and electrical conductivity were determined by electrode in 1 : 1 water solution , EPA 9045D; 2M KCl-extractable and water-extractable were measured in 1 : 10 soil extracts using continuous flow colorimetry (EPA 353.2, EPA 365.5); and particulate organic matter (0.5–2.0 mm) was measured by weight loss on ignition .|
For each set of paired soil cores in all treatments, one soil core was used to determine soil bulk density (, Mg m−3) from samples dried at 105°C for each depth increment. Soils from the second core were air-dried and passed through a 2 mm mesh sieve for all other soil physical and chemical analyses. Soil organic C and total N were measured by dry combustion (Vario Max CHN, Elementar, Hanau, Germany). Soils were combusted at 600°C to avoid release of soil inorganic C, which constituted approximately 13% of total C in surface soils to as much as 80% in deeper soils (data not shown). Soil stocks of SOC and total N (0–45 cm; Mg C or N ha−1) were calculated by depth increment using measured bulk densities and summing over all increments. Dry combustion at 600°C was also used to measure total organic C in biosolids grab-samples.
Water-stable aggregates were determined using the single sieve method  using soil aggregates in the 1-2 mm size range for 0–5, 5–10, 10–15, 15–25, and 25–35 cm depth increments. Aggregates in this size class were isolated by retaining 2 mm sieved air-dried soil passed through a 1 mm mesh sieve. Air-dried aggregates were prewetted with a fine mist for 1 hr using a commercial humidifier prior to direct immersion at a rate of 35 times per min for 3 min. The fraction of initial soil mass remaining was considered water-stable, and values were converted to a mass-per-area basis using soil bulk densities for each soil depth and summed for total water stable aggregates in the entire 0–35 cm soil depth.
Soil water characteristic curves were developed for 0–5, 5–10, 10–15, and 15–25 cm soil increments to evaluate management impacts on near-surface soil hydraulic properties. Air-dried soils from 3 to 5 replicate cores were wetted to a range of different volumetric water contents (~0.04 to 0.20 m3 m−3), sealed for a 24–36 hr equilibration period, and then measured for soil matric potential using a chilled-mirror dewpoint psychrometer (WP4-T, Decagon Devices, Pullman, WA) calibrated with a certified 0.1 mol kg−1 KCl salt solution. Nonlinear equations were fitted to measured data using a power function. Fitted equations were used to estimate soil volumetric water content (m3 m−3) at permanent wilting point (PWP) and field capacity (FC) for soil matric potential values of −1.5 MPa and −0.033 MPa, respectively. Available water capacity (AWC; m3 m−3) was defined as the difference in volumetric water content between FC and PWP.
2.3. Statistical Analyses
The absence of field replication in this municipally designed land-application operation precluded the use of analyses of variance to evaluate results. Instead, effects of biosolids application rate (0, 20, 40, and 60 Mg dry biosolids ha−1 yr−1 for 8 years) on measured soil physical and chemical properties were evaluated using regression analyses. Linear regressions were fit to data unless significant lack-of-fit indicated that a nonlinear regression was necessary. The effect of biosolids application duration was assessed for differences between 8 yr and 20 yr of application at 20 Mg dry biosolids ha−1 yr−1 using two-tailed -tests for groups with unequal variances. Means were considered different at the 0.05 significance level. To explore potential relationships between and SOC with WSA and AWC, percent values for SOC (soil concentration) and WSA (% mass remaining) were used instead of stocks per unit area to avoid autocorrelations between these metrics and . Statistical tests were conducted using SAS 9.3 (SAS Inc., Cary, NC).
3. Results and Discussion
3.1. Soil Organic Carbon and Total Nitrogen Stocks
To assess the extent to which surface-applied biosolids affected SOC and total N with soil depth, SOC and total N stocks were evaluated to a 45 cm soil depth in this study, deeper than most published studies on surface-applied biosolids. Here, surface application rates were positively correlated with SOC and total N in the top 15 cm soil layer, somewhat deeper than other studies reporting that SOC and N gains are limited to the top <10 cm of soils [24–27]. The current results underscore the fact that the effects of application rate and duration on SOC and total N stocks can be highly variable and depend on biosolids-specific composition as well as site-specific factors (e.g., soils, management) [5, 7, 28].
When examined for the entire profile depth sampled (0–45 cm), soil stocks of SOC increased nonlinearly with application rate after 8 yr of continuous annual applications (Figure 1(a)). A previous study using laboratory incubations to evaluate C and N mineralization responses in these soils reported similar increases in SOC (32 to 92%) in 0–10 cm soils treated with biosolids relative to untreated control soils . Other field studies on repeated surface-applied biosolids also have found increases in SOC [4, 12, 24–27, 29] and found that increases are positively correlated with application rate [4, 25]. Site-specific increases in SOC have been reported for application rates as low as 2 to 7 Mg ha−1 yr−1 [24, 30]. Field studies following a single application of surface-applied biosolids also report increases in SOC [8, 30–33].
Long-term applications of 20 Mg biosolids ha−1 yr−1 over 20 yr resulted in a 36% increase in SOC stocks compared to the 8 yr treatment at the same rate (Figure 1(a)). In contrast, Gaskin et al.  reported that SOC levels were not different between bermudagrass fields receiving repeated surface applications for <6 yr or for >6 yr, though SOC levels in both treatments were higher than unamended fields. Long-term gains in SOC have been reported in other studies which found that increased SOC or SOM levels can persist up to 27 yr after biosolids applications have ceased [24, 25, 29, 34–36].
Soil total N stocks (0–45 cm) followed similar trends to SOC, increasing nonlinearly with biosolids application rate (Figure 1(b)). In soils treated with 20 yr of biosolids applications at the lowest rate, total soil N stocks were 32% greater in long-term treated fields compared to midterm fields. In midterm fields, increasing application rates resulted in greater relative increases in total N stocks compared to SOC stocks. Higher enrichment in total N compared to SOC following biosolids application is well documented [5, 22, 25, 32, 33, 37] and could increase the risk of potential N losses by increasing direct N inputs and by stimulating organic N mineralization [5, 38]. Using laboratory incubations from soils at this site, Jin et al.  found that biosolids applications resulted in more volatile fluctuations in potential N mineralization and immobilization in surface soils (0–10 cm) amended at the two higher application rates but not in midterm or long-term soils applied at the lowest rate relative to control soils. A more recent study, however, reported elevated soil nitrate-N concentrations throughout the whole soil profile (0–110 cm) in all biosolids-treated fields compared to unamended control . Further, nitrate-N concentrations were >25 mg N kg−1 in subsoils deeper than 50 cm and were potentially below the predominant rooting zone, indicating an increased risk of N leaching losses . In contrast to these findings, a recent literature review reported that increases in soil organic N with repeated organic matter inputs can enhance long-term availability of N to crops, often without resulting in greater nitrate leaching to groundwater .
Mean values for soil C : N decreased linearly with increasing biosolids application rates, from in unamended control soils to , , and for 20, 40, and 60 Mg ha−1 yr−1, respectively (Figure 1(c)). Soils under long-term application had a C : N of , similar to control soils. Measured soil C : N values were within the range of reported values following biosolids applications [6, 24, 33, 37, 39] and followed expected decreases in C : N values associated with increasing rates or repeated applications of biosolids .
3.2. Soil Bulk Density
Soil bulk densities () for individual soil depth increments were generally similar across application rates, except in 5–10 cm soils where tended to increase with biosolids application rate (Table 3, Figures 3(a) and 3(b)). For the 20 Mg biosolids ha−1 yr−1 rate, long-term applications improved (e.g., decreased ) in the two surface soil increments (0–5 cm, 5–10 cm) compared to the midterm treatment. When aggregated to 0–45 cm depth, however, were similar between control and biosolids-amended soils. Earlier studies for soils from this site report contrasting effects of biosolids additions on . Jin et al.  reported no effects of biosolids applications on in 0–10 cm soils. Haney et al.  found that in 0–30 cm soils increased with application rate, presumably as a result of higher wheel traffic required to land-apply at greater biosolids rates, but not with application duration at the lowest rate . Results from the current study and previous reports are consistent with the variability in soil responses found in other studies on surface-applied biosolids which have reported no effects or increased [12, 32, 33, 40] or decreased due to biosolids application [24, 27].
In contrast, decreases in following the incorporation of biosolids into soils are reported commonly [4, 6, 9–11, 13, 16, 41–43]. The physical mixing of soils alone decreases . Depending on application rate, the incorporation of biosolids can further contribute to lowering by diluting soil mineral fractions with biosolids organic matter (OM) and subsequently increasing soil microporosity [9, 10, 13]. Surface broadcasting biosolids at this no-till perennial forage production site limited the impact of physically disturbing and homogenizing biosolids with surface soils. Changes to , therefore, could be attributed to wheel traffic and other management practices associated with forage production. The absence of changes with application rate observed here could be a result of the breakdown of biosolids into fine powder over time (and, in this case, with increased wheel traffic), which would limit changes to compared to more discrete biosolids aggregates . Improvements in in the long-term field relative to the midterm field also suggest that biosolids applications at the lowest rate can result in improvements in this specific soil physical quality metric.
3.3. Soil Water-Stable Aggregates
Water-stable aggregates (WSA) as a percent of whole soil decreased with increasing application rate in midterm applied fields at all measured soil depths relative to unamended controls. When converted to a mass-per-area basis, soil WSA decreased linearly with application rate at each soil depth and for the full 0–35 cm profile (Figure 2). Soil WSA was also lower in long-term applied fields compared to the midterm fields at the 20 Mg ha−1 yr−1 application rate, but in the 0–5 cm soil increment only (Figure 2(a)). Long-term decreases in soil WSA in near-surface soils also resulted in overall decreases in WSA observed for the full 0–35 cm profile (Figure 2(f)).
Organic amendments such as biosolids tend to increase soil physical fertility primarily by improving aggregate stability . Measurement of water-stable aggregates specifically addresses the potential for soil loss by water erosion and the potential to maintain soil structure which affects the transmission and retention of water. While organic amendments can increase soil aggregate stability by 1- to 10-fold, stability responses vary both spatially and temporally [4, 9, 11, 13, 15, 44]. Stability will also be affected by application rate and frequency, though aggregate stability is not always positively correlated with application rate . Greater plant growth and soil biological activity associated with organic matter additions are the key to increasing aggregate formation and stability. Organic inputs from aboveground (e.g., plant litter) and belowground (e.g., root litter and exudates, microbial turnover and exudates) are essential for aggregate cohesion or water repellency [6, 11, 25, 31–33, 39, 41]. Despite reported increases in microbial activity  and greater forage yields with increasing biosolids additions (J. Slagle, personal communication), WSA at all soil depths and for whole soils (0–35 cm) decreased with application rate and duration, in contrast to the majority of studies finding increases in aggregate stability after biosolids additions.
Both no change and variable changes in aggregate stability have been reported in surface-applied and incorporated biosolids studies [13, 16, 40, 43]. Only few studies have reported decreases in aggregate stability following additions of biosolids, animal manure, or other organic amendments [44–46]. Degradation of aggregates and decreased stability may be due to biosolids composition, specifically the increase in compounds directly or indirectly involved in the dispersion of fine soil particles. Dispersive agents in biosolids include humic substances [10, 45], anionic and nonionic surfactants , and high amounts of , K+, and/or organic P [14, 44]. While the composition of organic compounds in biosolids used here is beyond the scope of this study, a recent study reported that extractable K in these soils is not affected by biosolids rate or duration but that mineralization of organic P likely has contributed to high ortho-phosphate levels in the top 30 cm of soil . In addition, soils at this site are calcareous, and the presence of calcium carbonates is expected to contribute to flocculation and aggregation . Increases in biosolids-derived organic P, however, could bind to clay minerals and increase clay dispersion  or reduce the activities of or which are known aggregate bonding agents .
3.4. Soil Water Characteristics and Moisture Retention
Soil volumetric water contents tended to be higher at both permanent wilting point (PWP; −1.5 MPa) and field capacity (FC; −0.033 MPa) in biosolids-amended soils relative to unamended controls (Table 3). Values generally were within the range reported for fine-textured soils [4, 9, 40]. Despite relatively high values for soil moisture characteristic curves fitted to soils treated with the 60 Mg ha−1 yr−1 application rate, estimates of volumetric water content at FC were high at all soil depths, possibly due to the limited number of replicate cores used and/or high SOC levels. Available water capacity (AWC) also increased with biosolids application rate and, to a lesser extent, with increased duration of application. Changes in soil water characteristics in biosolids-amended soils were detectable to 35 cm depth, with the largest changes occurring in 0–10 cm surface soils.
Other studies have also found that surface-applied biosolids increase soil water retention at FC and PWP [27, 30, 37, 40]. Increases in soil surface area after OM addition may contribute to greater water retention at PWP  while increased microporosity enhanced water retention at FC . Increased soil water retention at PWP and/or FC has been found to be positively correlated with application rate in some cases [10, 30, 47] but not others [40, 48]. Changes in soil water retention, however, are soil-specific and are typically greater for coarser-textured soils compared to finer-textured soils such as those in the current study [9, 10, 30, 37, 40].
In the review by Kladivko and Nelson , small but nonsignificant increases in AWC occurred with surface-applied biosolids additions, though a more recent review of biosolids recycling studies in Washington, USA, showed variable effects of biosolids on AWC for a range of different textured soils . Improvements in water retention with no increases in AWC have also been measured in studies of incorporated biosolids [8–10]. These studies report AWC on a gravimetric basis, however, and changes in AWC are generally assumed to be nonsignificant on a volumetric basis . This contrasts with findings in this study that, even if AWC values from the highest application rate are omitted, biosolids additions enhanced volumetric AWC which also increased with biosolids application rate and duration.
3.5. Relationships between SOC and Soil Physical Properties
In general, biosolids applications tend to decrease , increase total porosity, and increase soil moisture retention primarily through addition of biosolids-derived organic matter [5, 6, 10, 11, 13, 42, 47]. In addition to enhancing organic C inputs to the soil, added organic matter improves (e.g., decreases ) by increasing the proportional distribution of micropores involved in water storage (0.5–50 μm) and transmission (50–500 μm) [10, 13]. Increases in microporosity subsequently can lead to increased soil water retention and improvement of other soil hydraulic properties. In this system, however, improvements in soil physical properties and SOC due to biosolids application could be offset by increased wheel traffic required to apply higher rates.
In this study, expected decreases in soil and increases in WSA (% mass remaining) associated with greater SOC concentrations (%C) were not observed (Figures 3(a)–3(c)), but increased SOC was linked to greater soil AWC (Figure 3(d)). Soil was generally unchanged by biosolids application rate in the midterm, but long-term improvements in were not associated with greater WSA or AWC in either surface soil increment (0–5 cm, 5–10 cm). Further, neither midterm nor long-term increases in SOC ameliorated biosolids management impacts on WSA, which generally declined in all biosolids-amended soils.
Land applying biosolids can serve multiple functions in addition to the beneficial reuse of wastes, including replacement of commercial fertilizers for crop production, improvement of soil condition, and storage of organic carbon in managed soils. In this study, we demonstrated that surface applications of biosolids can enhance SOC levels and improve soil hydraulic properties. Measured increases in SOC with application rate, however, were not associated with improvements in soil bulk density or soil aggregate stability reported in many other studies. Even under long-term application at the lowest rate where SOC increased and improved, degradation of soil WSA still occurred. These results demonstrate the potential for carbon storage in soils treated with surface-applied biosolids, but the contrasting effects of biosolids applications on soil physical properties underscore the importance of site-specific management decisions to minimize costs and maximize benefits associated with recycling biosolids in agricultural settings.
Mentioning of trade names or commercial products in this paper does not imply recommendation or endorsement by the U.S. Department of Agriculture.
Conflict of Interests
The authors declare that there is no conflict of interests regarding the publication of this paper.
This project was supported by the Agriculture and Food Research Initiative Competitive Grant no. 2008-35101-04440 to J. G. Arnold from the USDA National Institute of Food and Agriculture. The authors thank K. Anderson, D. Greene, J. Slagle, and D. White from the study site for their cooperation and E. Janacek for field and laboratory assistance. USDA is an equal opportunity provider and employer.
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