Urban construction sites usually result in compacted soils that limit infiltration    and plant growth   . Reduced infiltration can result in ponding or runoff and erosion    . Whereas the results of most studies suggest that surface runoff and associated losses of nutrient are less than those from agriculture, the most critical factor affecting runoff is management  .
Various management practices have been developed to restore urban soil qua- lity  . For example, Singer et al.  noted that using an aerator combined with surface compost additions improved infiltration and plant growth. Olson et al.  observed that compost additions to compacted soil decreased bulk density and increased infiltration. Likewise, Faucette et al.  observed significantly reductions in runoff, sediment, and nitrate loss when compost was applied to urban soils.
The rate of compost addition should be high enough to aid plant growth, but not so great that excess nutrients are lost in runoff or leachate    . John- son et al.  did not observe any significant increases in total phosphorus or nitrate loss for compost additions up to 99 m3∙Ha−1 (~1 cm thick) on bluegrass. Likewise Loper et al.  did not observe significant increases in nitrate leaching after additions of composted dairy manure (~0.5 cm thick) to turf; however, the compost increased nitrate leaching under ornamentals.
In addition to compost, native prairie grasses  and forbs  have greater rooting depth than normal lawn mixtures. Therefore, our hypothesis was that compost addition, with or without short prairie grasses, would improve soil and environmental quality in urban soils. The purpose of this study was to determine if compost, aeration, and/or prairie grasses should remediate a simulated urban construction site by reducing compaction and improving soil and water quality.
2. Materials and Methods
2.1. Site Setup
We tested our hypothesis by conducting two experiments. In Experiment 1, we compared soil physical properties and runoff under simulated rainfall of compacted plots planted with typical lawn species to plots with added compost and planted with prairie grasses. In Experiment 2, we compared three compost appli- cation methods on compacted urban soils.
2.2. Experiment 1
A 15 by 25 m urban site was prepared for the project (latitude, longitude: 41˚41'4.312"N, 93˚35'29.143"W). Although not known at the time the project was started, the site contained 0.5 to 0.9 m of fill material added in 1997 (manuscript in preparation). RoundupTM was applied to the sod in the fall of 2007. After the sod died, the sod and surface soil were removed (between 0.12 and 0.3 m deep east to west), and the soil was stockpiled. Leaf and grass compost (Mulch Mart, Waukee, IA) was bought and covered with tarps for the winter. On 14 April 2008, the area was graded to 1% slope and the subsoil compacted by trafficking with a tractor.
On the control lawn half, topsoil was applied to 5 cm depth and rototilled in. On 12 May 2008, a commercial lawn mixture (C-3) was planted (30% Kentucky bluegrass Poa pratensis L., 40% perennial ryegrass Lolium perenne L., 30% creeping red fescue Festuca rubra L. ssp. rubra) was planted at a rate of 412 kg∙Ha−1. On 23 June 2008, fertilizer (6.4 kg of 10-20-10) was applied (170 kg∙ha−1).
On 8 May 2008, the other half of the area was remediated by using a tractor to pull a shallow (15 cm) homemade slotting tool (Figure 1) on the contour every 0.76 m. Five cm of the stockpiled topsoil and 10 cm of compost was applied to this remediated area and incorporated using a rototiller. The prairie grasses Buffalo grass (Buchloe dactyloides (Nutt.) Engelm.) and Blue Grama grass (Bouteloua gracilis H.B.K.) (C-4 grasses) were each planted on the treatment side (194 kg∙ha−1 each, 12 May 2008); however, the buffalo grass did not emerge well and was replanted 7 July 2008 by hand on the bare spots. The buffalo grass was seeded 0.3 cm deep with a rotary spreader. The blue grama grass seed was spread on the surface. Except for the compost, no fertilizer was applied to the remediated area. Both areas had straw applied 12 June 2008 to protect the soil.
On 8 July 2011, the original plots (Figure 1) were subdivided and half of each side was aerated first, and then top dressed with 1.27 cm of compost to replenish some of the original compost lost to decomposition or supply a small amount of compost to the control. The sites were periodically mowed, watered, and commercial fertilizer and weed killer were applied.
2.3. Experiment 2
On 8 to 9 July 2011, new smaller plots (3.05 by 3.05 m) were established adjacent and around the original plots (Figure 2). As was done for Experiment 1, the sod was killed with glyphosate (RoundupTM), and topsoil was removed and stockpiled. The plots were then graded to around 2% slope and then compacted by
Figure 1. Homemade soil slotting tool used in Experiment 1.
Figure 2. Layout of original plots (not to scale, total area 15 by 25 m), established 2008, split in 2011 with compost and aeration addition to half, and new plots (each 3.05 by 3.05 m) established 2011. Compost is given by cmp, aeration by aer, rototill by till. The area for both experiments included grassed areas between plots was 29 m east-west, and 24 m north- south.
driving over with a skid loader. There were four duplicated treatments. The control lawn treatment (Treatment 1) had 5 cm of topsoil spread on the surface. Treatment 2 had 5 cm of topsoil spread on the surface, then plug aerated with 5 cm of compost (Iowa State University Dairy Farm composted manure). Treatment 3 was rototilled first, and then covered with 5 cm of topsoil and 5 cm compost mixed. Treatment 4 had 5 to 7.5 cm of compost blanket spread on it. All treatments were hydromulched with a bluegrass mixture. The sites were periodically mowed, watered, and commercial fertilizer and weed killer were applied. For some years, grass seed was sprinkled in bare spots.
2.4. Rainfall Simulations
In August 2009, approximately 15 months after the topsoil and compost addition and planting of the original Experiment 1 plots, a rainfall simulator similar to that described by Byars et al.  was used to evaluate infiltration, runoff, and soil erosion in 1.22 × 2.44 m plots (one plot for each of the two treatments). The rainfall intensity was 72 mm・h−1, which was applied from eight Rain Bird 8-VAN (Rain Bird, Corp., Azusa, CA)1 nozzles that were located along the perimeter of the rainfall simulator at 2.43-m above the ground. The plots were constructed using steel borders that were inserted 6-cm deep along the sides and up-slope end. Runoff was collected at the down-slope end, where a V-shaped collector was placed above a collection trough. The V-shaped collector was inserted carefully to a depth that was level with the surface of the plot. Gaps present along this border were packed with soil excavated during the installation. Runoff from outside the plot was directed to two additional troughs located on each side of the center trough and was discarded. The runoff was measured every minute, and steady state conditions were assumed to have been established when runoff rates were constant for four consecutive minutes. Then runoff was collected every five minutes using a 30 s subsample. If the container became full before 30 s, the exact amount of time required to fill the container was recorded. Soil cores measuring 1.9-cm diameter × 30-cm length were collected to determine antecedent and post-rainfall soil water content for each plot. The soil cores for antecedent water content were taken adjacent to each plot, and for the post-rainfall soil were taken within each plot. This rainfall simulation was conducted on the lower west end of the plots where there was fill material that was darker than that on the lawn area than the compost/prairie grass area.
A follow-up rainfall simulation study was conducted 17-20 September 2012 on the upper east end of the plots. As described above, the Experiment 1 plots were subdivided with half receiving 1.27 cm of compost and aerated July 2011. The rainfall simulations were conducted on 1.5 m by 3 m plots, using the procedures and simulator described by Kovar et al.  . The plots were oriented to allow water to flow down to metal sheet plates at the bottom edge. The simulator delivered rain at 65 mm・h−1 determined from calibration. Time to runoff was recorded. Runoff samples were collected at 2.5, 7.5, 12.5, 17.5, 22.5, and 27.5 min after a steady-stream of runoff was established. Total runoff from each plot was weighed to determine the amount.
Sub-samples of runoff were filtered in the field through 0.45 μm cellulose acetate filter for ortho-P analysis. The rest of the runoff sample was mixed and sub- sampled for nitrate-N, total P, and sediment content. Measured concentrations were corrected by subtracting concentrations in the water used for the rainfall si- mulation. Nitrate plus nitrite nitrogen was measured with a Lachet Autoanalyzer using a Cd reduction   . Total phosphorus was determined using flow injection analysis   after acid-persulfate digestion. Runoff subsamples were dried at 105˚C to determine sediment loss.
The rainfall simulator was too large to rain on individual Experiment 2 plots; therefore, the simulator was positioned so that two smaller (1.5 m × 1.5 m) side- by-side plots could be rained on simultaneously, one nozzle per plot (Figure 2 and Figure 3). Metal sheeting in a V-shape was used to collect runoff at the bottom edge. Runoff samples were collected as for the large plots, but samples were not saved for nutrient analysis.
2.5. Soil Water, Bulk Density, Morphology
Six undisturbed soil cores (7.4 cm diameter, 7.6 cm long) were collected to determine bulk density before soil disturbance related to construction of the Experimental 1 plots. Additional cores were taken in fall 2008 after disturbance and treat- ments had been imposed. For each treatment, five surface and subsurface cores
Figure 3. Rainfall simulation on side-by-side small plots in 2012. Note the tarp was used to block the wind and increase uniformity of simulated rainfall on the plots. Four small rain gages in each plot were used to assess the rainfall distribution.
were taken. The top of the subsurface depths were immediately beneath the surface-applied soil or compost.
Soil water content was monitored by measuring the real permittivity using a hydra probe (Stevens Vitel, Inc., Cantilly, VA) in all three studies. Experiment 1 was monitored in 2008 to 2010 (before the plots were subdivided and half were topdressed with compost), and 2012 to 2014 (after topdressing with compost). Experiment 2 was monitored 2012 to 2014. Three to ten spots were measured per treatment, using the calibration equation.
θ = −0.002 + 0.0608  , in which θ was water content and was the square root of the real permittivity.
On 26 October 2011, two undisturbed soil cores (73 mm diameter and 76 mm high) were taken from each of the Experiment 1 plots that had addition of compost with aeration for both the surface and sub-surface soil. Two soil cores were also taken in the split side of the original Experiment 1 plots without the new aeration compost top dressing treatment. This was to determine the effect of the small compost additions.
In May 2015, undisturbed soil core samples were collected in plastic tubes ~5 cm diameter. These were used to determine the remaining depth of the surface- applied treatments as indicated by soil color with value/chroma of 3/2 or darker.
The large plots of Experiment 1 were not replicated; however, for the rainfall si- mulation study (after subdividing the plots), we treated the two measurements (original and zones with additional compost and aeration within the plot) as replicates. The small plots of Experiment 2 were true replicates. Data were analyzed by analysis of variance, and treatment mean differences using Tukey’s Test. ANOVA and Tukey’s Test were also used to compare yearly differences in soil water content among treatments.
3. Results and Discussion
3.1. Experiment 1
3.1.1. Bulk Density
Bulk density before compacting the soil was 1.39 g・cm−3 for the soil surface. In 2008 (after the plots were compacted, prepared, and planted) the surface bulk densities were 1.45 g・cm−3 for the bluegrass lawn and 1.11 g・cm−3 for the prairie compost large plots, whereas subsoil bulk densities for both treatments were 1.73 g・cm−3. These results indicated that the compaction treatment was successful in increasing bulk density. Similarly, Gregory et al. (2006) showed urban compaction significantly increased bulk density. When topsoil was replaced, the bulk density was slightly higher than before compaction. Adding compost lowered the bulk density of surface soil compared to the original condition.
In 2011 (three years after the initial treatments), the surface bulk densities were 1.30 g・cm−3 and 1.17 g・cm−3 for the bluegrass lawn and for the prairie-grass compost large plots. These results suggest that reduction in bulk density due to compost addition can persist for at least 3 yrs. Subsoil bulk densities were 1.62 g・cm−3 and 1.48 g・cm−3 for the bluegrass lawn and for the prairie-grass compost large plots. For the compost treated plot planted with prairie grasses, this indicated a reduction in subsoil bulk density relative to the topsoil alone treatment and the initial post-compaction subsoil bulk density. Over time these deep-rooted grasses reduced traffic-induced subsoil compaction. Johnson et al.  observed topdressing compost onto turf resulted in significantly lower bulk density.
3.1.2. First Rainfall Simulation Experiment 1
The rainfall simulator study of 2009 (15 months after establishing the plots) showed steady-state infiltration rates of 51.4 and 32.5 mm・h−1 for the lawn and for the compost/prairie grasses treatment. The sediment loss rate was 93 kg・ha−1・h−1 for the lawn/control, but there was no measureable sediment loss from the compost/na- tive grasses treatment despite having greater runoff rate (40 vs. 21 mm・h−1). The soil water increase from the rain was 12.2 and 21.0 mm for the top 0.3 m depth of the lawn/control and the compost/native grasses treatment. Water contents before the applied rainfall were similar for the two treatments. The summary from the first rainfall simulation is that the lawn/control had greater infiltration rate and less runoff than the compost/prairie grassed, but more sediment loss. More of the simulated rainfall was retained in the upper 0.3 m of the compost-amended prairie grass plot than the lawn treatment.
3.1.3. Second Rainfall Simulation
When the second rainfall simulations were conducted in 2012, the grasses were well-established and the main plots had been subdivided (half of each receiving compost and aeration, Figure 2). When the two halves were treated as replicates (Table 1), the prairie-grass compost area compared with the bluegrass mix had significantly faster infiltration rate, slower runoff acceleration rate, less sediment loss, and reduce ortho-P and total P minus ortho-P loads. This rainfall simulator study was conducted on the east section of the plots where there was less treatment difference for depth of surface dark fill material. For both treatments, nitrate levels were at or below the concentrations in the supply water and are not reported.
Others show that urban compaction significantly reduces infiltration rates (i.e.  ). Time to runoff for grass generally ranges from 2 to 15 min   . Sediment loss from grass can range from 10 to 180 kg・ha−1 over 35 min  , or from 0.1 to 104 kg・ha−1 per event of 12 to 30 min duration  . In our study, the soil was initially-dry and slopes were less-steep than for studies in the literature; therefore, we showed increased time to runoff compared with literature studies. Faucette et al.  observed that runoff and sediment loss from construction areas were reduced 3 months after applying poultry manure with other amendments.
Our P losses in runoff were at the low end for grassland, probably due to the small slopes in this study. Previous studies of P loss in runoff from grassland showed soluble P concentration ranging from 0.1 to 2.3 mg・L−1  , and soluble P load ranging from 0.3 to 2.1 kg・ha−1  . Total P concentrations in runoff can range from 0.3 to 7.1 mg・L−1  , and total P loads can range from 0.4 to 2.5 kg・ha−1  .
3.1.4. Soil Water Range of Difference
The compost treatment held water more readily than the lawn treatment without compost. The range of difference for soil water content 2008 through 2010 was 0.180 and 0.235 m3・m−3 for the control lawn and improved (compost + prairie grass).
Table 1. Rainfall simulator results (2012) and soil sampling as influenced by lawn treatments for Experiment 1.
Means followed by the same letter within a row are not significantly different at p = 0.05 by Tukey’s test.
The range of soil water content 2013 was 0.038, and 0.194 m3・m−3 for control and improved areas, which was significantly different. A larger range suggested better water holding capacity for the improved area. The differences in 2014 were not significant: 0.102 and 0.181 m3・m−3 for the control or improved areas. In general, water content was related to time of year since C-3 lawn grasses are more active in the spring and fall, and warm season C-4 blue gamma grass is more active in the summer (not shown).
Other researchers have investigated the effect of compost additions on soil water. Johnson et al.  did not observe any effect of topdressing compost onto turf on soil water content. In contrast, Singer et al.  showed that compost increased soil water content at an urban site only soon after rain events, and soil water content was increased more when the compost was incorporated than for surface applications. Too much water can result in aeration problems on compacted soil  .
3.1.5. Treatment Depth
Samples taken in 2015 (Table 2) showed that some of the original applied compost or topsoil (indicated by dark soil) was no longer visible, having been lost to settling and oxidation. When 1.3 cm of compost was added in 2011, the treatment depth effect was even greater at 5 cm. The compost with prairie grasses still showed 6 cm of treatment depth, but only 6.5 cm when 1.3 cm compost was added in 2011. Olson et al.  suggested that if compost plus tillage increased root growth, the roots themselves could provide continual soil structure improvement even as the compost degrades over time.
3.2. Experiment 2
3.2.1. Rainfall Simulation
The small plots showed the compost blanket treatment significantly increased the time to runoff compared with the no compost treatment, but there were no
Table 2. Soil inflence from applied treatments, 4 to 8 years later.
aTMT is treatment.
significant difference among treatments noted for the other runoff parameters measured (Table 3). As noted for Experiment 1, our runoff time was longer and sediment loss was lower than observed in other studies   probably due to small slopes in our study.
3.2.2. Soil Properties
Surface bulk density was significantly greater for the no compost treatment that for compost with aeration or compost with tillage (Table 2). The new control that only had topsoil added showed no dark soil left in 2015 (Table 3). The treatment with compost that had been rototilled showed dark soil over 8 cm deep.
3.2.3. Soil Water Annual Range of Difference
Higher bulk densities resulted in numerically higher water contents in the top 10 cm for the control lawn with no compost (Treatment 1) compared with other treatment (not shown). The ranges of water content for 2012 were 0.206, 0.214, 0.236, and 0.221 m3・m−3 for control, compost + aeration, compost + rototilled, and compost blanket. Similarly the water content ranges for 2013 were 0.110, 0.131, 0.123, and 0.118 m3・m−3 for the same treatments. Also for 2014 the range of water contents for 2014 were 0.163, 0.184, 0.076, and 0.134 m3・m−3 for the same treatments. None of these differences were significant, but the treatments that received compost tended to have higher differences in soil water content over the year. The higher difference in soil water content suggested a trend toward greater water holding capacity where the compost was added.
4. Conclusions and Recommendations
Compost reduced bulk density in the surface soil. Compost with prairie grasses
Table 3. Rainfall simluator and soil sampling results (2012) as influence by lawn treatments, Experiment 2.
a. The rototill-compost treatment is excluded from rainfall simulator analysis since one plot did not have runoff even after 2.8 hours. b. Means followed by the same letter within a row are not significantly different at p = 0.05 by Tukey’s test.
significantly increased infiltration and reduced runoff and sediment loss compared with bluegrass lawn. Compost additions made the surface soil darker than merely adding topsoil.
More than minimal compost additions showed some improved soil quality of post-construction soils. Although establishment was slow, the prairie grasses even- tually resulted in a dense sod that reduced runoff, and erosion, and surface P loss. Over time, the compost was decomposed, so periodic refreshment of a compost blanket would be recommended.
Thanks to Gavin Simmons for field data collection, Jeff Cook for rainfall simulator assistance, and Amy Morrow for analytical laboratory support.
 Kelling, K.A. and Peterson, A.E. (1975) Urban Lawn Infiltration Rates and Fertilizer Runoff Losses under Simulated Rainfall. Soil Science Society of America Proceedings, 39, 348-352.
 O’Neil, K.J. and Carrow, R.N. (1983) Perennial Ryegrass Growth, Water Use and Soil Aeration Status under Soil Compaction. Agronomy Journal, 75, 177-180.
 Knox, E.G., Bouchard, C.E. and Barrett, J.G. (2000) Erosion and Sedimentation in Urban Areas. In: Brown, R.B., et al., Eds., Managing Soils in an Urban Environment, Agronomy Monograph 39, ASA-CSSA-SSSA, Madison, 179-197.
 Faucette, L.B., Jordan, C.F., Risse, L.M., Cabrera, M., Coleman, D.C. and West, L.T. (2005) Evaluation of Stormwater from Compost and Conventional Erosion Control Practices in Construction Activities. Journal of Soil and Water Conservation, 60, 288-297.
 Maniquiz, M.C., Lee, S., Lee, E., Kong, D.-S. and Kim, L.-H. (2009) Unit Soil Loss Rate from Various Construction Sites during a Storm. Water Science Technology, 59, 2187-2196.
 King, K.W. and Balogh, J.C. (2008) Nutrient and Pesticide Transport in Surface Runoff from Perennial Grasses in the Urban Landscape. In: Beard, J.B. and Keens, M.P., Eds., Water Quality and Quantity Issues for Turfgrasses in Urban Landscapes, Chapter 8, Council for Agriculture Science and Technology, Ames, 121-152.
 Adamson, D., Bazter, D., Foster, A., Griffin, J., Kauten, R., Masteller, M., Petersen, W., Pierce, G., Sauer, P., Stineman, B. and Welch, J. (2014) Section 2E-6-Soil Quality Management and Restoration. Iowa Stormwater Management Manual, 1-20.
 Singer, J.W., Malone, R.W., Tomer, M.D., Meade, T.G. and Welch, J. (2006) Compost Effect on Water Retention and Native Plant Establishment on a Construction Embankment. Journal of Soil and Water Conservation, 61, 268-273.
 Olson, N.C., Gulliver, J.S., Nieber, J.L. and Kayhanian, M. (2013) Remediation to Improve Infiltration into Compact Soils. Journal of Environmental Management, 117, 85-95.
 Linde, D.T., Watchke, T.L., Jarrett, A.R. and Borger, J.A. (1995) Surface Runoff Assessment from Creeping Bentgrass and Perennial Ryegrass Turf. Agronomy Journal, 87, 176-182.
 Glanville, T.D., Persyn, R.A., Richard, T.L., Laflen, J.M. and Dixon, P.M. (2004) Environmental Effects of Applying Composted Organics to New Highway Embankments: Part 2. Water Quality. Transactions of ASAE, 47, 471-478.
 Saebo, A. and Ferrini, F. (2006) The Use of Compost in Urban Green Areas—A Review of Practical Application. Urban Forest and Urban Greening, 4, 159-169.
 Johnson, G.A., Davis, J.G., Qian, Y.L. and Doesken, K.C. (2006) Topdressing Turf with Composted Manure Improves Soil Quality and Protects Water Quality. Soil Science Society of America Journal, 70, 2114-2121.
 Loper, S.J., Shober, A.L., Wiese, C., Denny, G.C. and Stanley, C.D. (2013) Nutrient Leaching during Establishment of Simulated Residential Landscapes. Journal of Environmental Quality, 42, 260-270.
 Mahaney, W.M. (2010) Plant Controls on Decomposition Rates: The Benefits of Restoring Abandoned Agricultural Lands with Native Prairie Grasses. Plant and Soil, 330, 91-101.
 Kovar, J.L., Moorman, T.B., Singer, J.W., Cambardella, C.A. and Tomer, M.D. (2011) Swine Manure Injection with Low-Disturbance Applicator and Cover Crops Reduce Phosphorus Losses. Journal of Environmental Quality, 40, 329-336.
 Wood, E.D., Armstrong, F.A.J. and Richards, F.A. (1967) Determination of Nitrate in Seawater by Cadmium-Copper Reduction to Nitrite. Journal of the Marine Biological Association of the United Kingdom, 47, 23-31.
 Tomer, M.D., Moorman, T.B. and Rossi, C.G. (2008) Assessment of the Iowa River’s South Fork Watershed: Part 1. Water Quality. Journal of Soil and Water Conservation, 63, 360-370.
 U.S. Environmental Protection Agency (1993) EPA 365.1: Determination of Phosphorus by Semi-Automated Colorimetry, Revision 2.0.
 U.S. Environmental Protection Agency (1978) EPA 365.3: Phosphorous, All Forms (Colorimetric, Ascorbic Acid, Two Reagent).
 Logsdon, S.D. and Hornbuckle, B. (2006) Soil Moisture Probes for Dispersive Soils. 3rd International Symposium and Workshop on Time Domain Reflectometry for Innovative Soils Applications, West Lafayette, 17-20 September 2006, Paper No. 13.
 Krenitsky, E.C., Carroll, M.J., Hill, R.L. and Krouse, J.M. (1998) Runoff and Sediment Losses from Natural and Man-made Erosion Control Materials. Crop Science, 38, 1042-1046.
 Ramirez-Avila, J.J., Stomayor-Ramirez, D., Martinez-Rodrguez, G.A. and Perez-Aegria, L.R. (2011) Phosphorus in Runoff from Two Highly Weathered Soils of the Tropics. Canadian Journal of Soil Science, 91, 267-277.
 Franklin, D.H., Cabrera, M.L. and Calvert, V.H. (2006) Fertilizer Source and Soil Aera-tion Effects on Runoff Volume and Quality. Soil Science Society of America Journal, 70, 84-89.