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Modeling Plume-Rise of Air Emissions from Animal Housing Systems: Inverse AERMOD

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DOI: 10.4236/jep.2017.811078    561 Downloads   1,022 Views  

ABSTRACT

As fate and transport of air emissions from animal housing systems is of increasing concern, dispersion models have become commonly used tools to estimate the downwind concentrations of pollutants at certain locations surrounding the animal production farms. In application of Gaussian dispersion model for downwind concentration predictions of animal housing emissions, unknown plume rise (△h) and plume shape of the horizontally emitted plumes from animal housing systems have been vital weak points challenging the accuracy of the model predictions. This paper reports an inverse AERMOD modeling study to derive the plum rises of PM10 emissions from mechanically ventilated egg production houses based upon field measurements of PM10 emission rate, downwind concentrations, and meteorological conditions. In total, 87 hourly plume rises were found for 20 days (five days per season for four seasons, from fall 2008 to summer 2009). The mean plume rises for fall 2008, winter 2008, spring 2009 and summer 2009 were 16.2 m (SE = 11.2 m), 7.9 m (SE = 9.5 m), 16.5 m (SE = 12.4 m), and 14.3 m (SE = 10.0 m), respectively. The relationships between plume rises and various factors were tested. While the diurnal patterns of the plume rises were not consistent among different selective days, they generally followed the diurnal patterns of house ventilation rates. Plume rise for weekends were significantly higher than those for weekdays in fall. Multiple linear regression showed a significant positive relationship (p = 0.0134) between wind speed and the plume rises. Ambient relative humidity and total volume flow were also found to be slightly (p = 0.171 and 0.217, respectively) related to the plume rises.

1. Introduction

Animal feeding operations (AFOs) emit significant amount aerial pollutants, contributing to the elevated air pollutant concentrations in the vicinity areas [1] - [9] . Although air emissions from AFOs are of great environmental concern in the United States (U.S.), application of the current National Ambient Air Quality Standards (NAAQS) is challenged due to lack of knowledge about air dispersions of AFO air emissions. Fate and transport of air emissions from AFO facilities have become a growing political and environmental concern [10] [11] [12] .

In the studies of AFOs air emissions, atmospheric dispersion models are often used to predict downwind concentrations of the emitted pollutants [13] - [19] , or, to derive emission rates through inverse modeling [20] - [26] . Among various types of dispersion models (e.g., Box models, Gaussian models, Lagrangian and Eulerian models, and CFD model) [27] , Gaussian plume models are the most widely used for numerically describing dispersion of air emissions from different types of sources (e.g., point, line, area, volume; or, industrial stacks versus agricultural operations; etc.) [28] [29] [30] [31] . In application of the Gaussian dispersion models, knowledge about plume-rise is required for simulating the dispersion of the plume and calculating the concentrations at downwind locations [28] [32] [33] [34] . By definition, plume rise is the rise of the dispersing plume centerline above its original emission source height (i.e., the physical stack height). In the literature, dispersion plume rises from various emission sources have been experimentally studied [35] - [42] and several plume rise models were developed from observations of emission plumes from industrial stacks (Figure 1(a) & Figure 1(b)) with both vertical momentum and thermal buoyancy [32] [43] [44] [45] [46] [47] . In modern animal production houses, mechanical ventilation systems are used to create optimal growing conditions for animals. Aerial pollutants from those houses are usually released through ventilation fans at ground level and horizontal positions or positions slightly tipping downwards (Figure 1(c)). There is no actual emission “stack”, nor is there upward vertical velocity. As a result, the current plume rise models do not apply for AFO air emission dispersion modeling. Unknown plume-rise and plume shape (i.e., horizontal and vertical plume spread parameters) are vital weak points challenging the accuracy of the Gaussian model predictions.

Figure 1. Visual comparison of various emission plumes. (a) Power plant stacks, Source: http://www.epa.gov/airmarkets/participants/monitoring/index.html; (b) Industrial stack; (c) Emission plume from two tunnel ventilated poultry houses (image by Wang-Li).

As a preferred regulatory air dispersion model of the U.S. Environmental Protection Agency (EPA), AERMOD was developed by the American Meteorological Society (AMS) and EPA Regulatory Model Improvement Committee (AERMIC) in early 1990’s. This AERMIC Model (i.e., AERMOD) was a replacement of the previous regulatory model ISCST3. Like ISCST3, AERMOD is a Gaussian-based model that incorporates advanced understanding of the boundary theory and turbulence with inclusion of terrain interactions [48] [49] [50] . In AERMOD, at stable conditions, the plume dispersion is treated as Gaussian distribution in both vertical and horizontal directions; the plume rise is determined by Briggs equations [48] [49] that takes temperature and wind changes above stack top into consideration. At unstable conditions (convective conditions), the plume dispersion is treated as Gaussian distribution in horizontal direction and as bi-Gaussian probability distribution in vertical direction; the plume rise is determined using convective plume rise formulations that account for convective updrafts and downdrafts [48] [49] . Although AERMOD is far more advanced than other Gaussian-based models, it still shares the deficiency in assessing the plum rise for emission sources with ground level and horizontal emission characteristics as it is of animal housing emission. Since AERMOD has been adopted by the State Air Pollution Regulatory Agencies (SAPRAs) to predict downwind concentrations or to derive emission rates through inverse modeling, and/or to compile emission inventories for agricultural emission sources, it is essential to develop understand the dynamics of the plume rises of agricultural air emissions as impacted by the production practices and atmospheric conditions. Therefore, the objectives of this research were to apply inverse-AERMOD to derive the plume rises of animal house air emissions using field measurements of particulate matter (PM) emissions and downwind concentrations; and to identify the impacts of various factors on plume rises from the animal houses based upon the inverse-AERMOD results and the field observations.

2. Materials and Methods

In this study, plume rises for animal housing systems were predicted using inverse AERMOD approach. The PM10 dispersion from a commercial egg production farm was modeled based upon measured emission rates. The plume rises for the source types (i.e., ventilation types) were adjusted and the results of model predicted hourly downwind PM10 concentrations were compared with field observations at four ambient stations in the vicinity. When the model prediction agreed with the field measurement within ±20% relative difference, the plume rise for that given hour was considered valid. In total, 480 hourly PM10 data for four seasons with five days per season for four seasons were selected for this modeling study.

2.1. The Egg Production Farm and the PM10 Monitoring Station

The PM data collection was conducted on a commercial egg production farm in North Carolina. As shown in Figure 2, this farm consisted of nine layer houses and an egg packing building. Based on the house type and ventilation type, the production houses were grouped into (1 tunnel ventilated high-rise layer houses (houses 1 - 4); (2 cross ventilated high-rise layer houses (houses 5 - 6); and (3 naturally ventilated shallow pit layer houses (houses 93, 102 - 103). In the high-rise houses, laying hens were caged on the second floor in 6 rows (houses 1 - 4) or 8 rows (houses 5 - 6) and manure was stored in the first floor and was completely cleaned out once a year. In the naturally ventilated houses, hens were caged in 4 tires and manure was flushing out to lagoons twice a day. The dimensions of the houses are listed in Table 1.

The tunnel ventilated houses used 17 belt-driven ventilation fans (upper 8 and lower 9, 1.22 m in diameter) on end wall of each house (Figure 3). The cross- ventilated houses had 27 belt-driven ventilation fans (1.22 m in diameter) arrayed on each side wall of each house (Figure 3). The naturally ventilated had curtain openings on the side walls, and twenty winter vents evenly distributed on the building ridge.

The PM concentrations were monitored at 5 locations, of which one was the in-house monitoring station (ST1 in Figure 2) and 4 were ambient monitoring

ST1 = station 1 (inside the house 4); ST2 = station 2; ST3 = station 3; ST4 = station 4; ST5 = station 5

Figure 2. The egg production farm layout and the PM10 monitoring stations [51] .

Table 1. Building information of the production houses.

Figure 3. Illustration of the fans in tunnel-ventilated houses (top) & a cross-ventilated house (bottom).

stations (ST2-5 in Figure 2). The ST1 was designed to measure in-house PM concentration for determination of PM emission rate from the tunnel ventilated houses, whereas ST2-5 were designed to simultaneously measure downwind and upwind PM concentrations. Also, there is another PM monitor at the ventilation air inlet of house 4, measuring the background PM concentrations of the house inlet air. At each PM monitoring station, one tapered element oscillating microbalance (TEOM) equipped with a federal reference method PM10 sampling head was used to take continuous PM10 measurements [5] [51] . A 10 m weather tower with sensors for solar radiation, wind speed and direction, ambient temperature and relative humidity (RH) were used to take onsite meteorological measurements at one minute interval.

In this study, dispersion modeling was conducted based upon hourly measurement data for four periods with each period having consecutive five days from fall 2008 to summer 2009. Dates with rainfall, snowfall or other unusual conditions (e.g., instrument calibration dates) were excluded. The selection of the five days was set to be the periods with the least data points being excluded. In total, 435 valid hours were finally selected for the modeling practices.

2.2. AEROMOD Simulation

2.2.1 PM10 Emission Rate Determination

For tunnel-ventilated houses, the PM10 emission rate (ER) of house 4 was calculated based upon field measurements of PM10 concentration and house ventilation rate using Equation (1) [5] The ERs from other three tunnel houses (1 - 3) were assumed to be the same as it from the house 4 since these four houses were identical in building configurations, ventilation system controls, production management practices, and hen types/ages/populations

E R = C Q (1)

where

ER = emission rate of the PM10, μg s−1

C = PM10 concentration at the source (ST1), μg m−3

Q = ventilation flow rate of individual fan, m3 s−1

For cross-ventilated houses, since they shared the same production management practice with the tunnel-ventilated ones, also because they housed 2 additional row of caged laying hens as compared to the tunnel houses (8 rows versus 6 rows), the emission rate of cross-ventilated ones were assumed to be 8/6 times the emission rate of tunnel-ventilated houses.

For naturally ventilated houses, the ERs would be much less because of wet base manure management practice. Thus, it was assumed that the PM concentrations were 80% of the PM concentrations at the first floor of the tunnel ventilated houses for spring, summer and fall times. The ventilation of naturally ventilated houses was basically through the curtains on the side walls. The air flow velocity (V) was assumed to be the same as the wind speed vector in the direction perpendicular to the side walls of the naturally ventilated houses. The curtains were assumed to be fully opened for summer times, half opened for spring and fall times and fully closed in winter times. For winter times, the 20 ridge vents of the houses 102 & 103 were of the exhausts for air emissions. The house 93 did not have vents on the ridge, the emission from this house was insignificant in winter times, therefore, the ERs from houses 102 and 103 in winter times were computed by the following equation:

E R n a t . = f 1 f 2 f 3 E R t u n . (2)

where

f1 = factor due to wet base = 0.8

f2 = factor due to ventilation = 0.4

f3 = factor due to population = 70,000 hens in house 102 & 103/96,000 hens in house 4

ERtun = total emission rate in tunnel ventilated house, ug s−1

2.2.2. Source Inputs

Each fan in the mechanical ventilation systems was considered as an individual horizontal point source. The emissions from side wall curtains of the naturally ventilated houses in spring, summer and fall were considered as area sources; whereas in winter time the 20 ridge vents were considered as 20 capped point sources for houses 102 and 103. The stack heights and stack diameters of point sources were determined based upon the fan diameter and locations (Table 2).

Table 2. Stack heights and stack diameters for point sources.

[a]Rectangular vents with an area of 1.86 m2. A stack diameter of 1.54 m was used as it provides a same area.

The stack velocities for horizontal point sources were computed by Equation (3):

V = Q 4 π D s 2 (3)

where Ds = the stack (fan) diameter

Q = ventilation flow rate of individual fan, m3 s−1

For naturally ventilated houses, the dimensions of the opening of the curtains were the dimension of the area source. For capped point sources, the stack velocities were assumed to be the same as wind velocities; for area sources, the exit velocities were assumed to be the wind velocities in the direction perpendicular to the side walls.

2.2.3. Plume-Rise Prediction

After completion of all the input files, hourly AERMOD simulations were conducted to derive plume rises for the selected data periods specified in Table 3. These hourly simulation followed the processes in the following diagram.

In Figure 4, the RD was compute by comparing the model predicted data (∆Cp) with the field measurements (∆Cm) using Equation (4):

Table 3. Data periods selected for modeling PM10 dispersion to derive plume rises through inverse AERMOD method.

Figure 4. Flow chart of inverse-AERMOD modeling in predicting plume rises [52] .

RD: relative difference between model production and field measurement; ∆Cm: measured PM10 concentration at the receptor (downwind minus upwind); ∆Cp: modeled PM10 concentration at the receptor; ∆h: plume rise.

R D ( % ) = | Δ C p Δ C m | Δ C m (4)

2.3. Data Analysis

After all the hours were run and the ∆hs were determined, seasonal, diurnal and weekly changes of plume rises were then analyzed. As the magnitude of plume rises may be affected by wind direction, wind speed and the temperature differences between ambient and the emission plume flow, these factors were chosen for multiple linear regression analysis. Also, the cloud cover and solar radiation were closely related to the stability class of the ambient environment, and were thus taken into consideration as influencing factors (predictors). Since momentum and thermal buoyancy had been the most important factors affecting plume rises, the total volume flow of the exhaust fans was then chosen to represent the momentum of the source. After selecting the possible factors affecting plume rises, a multiple linear regression analysis was conducted to identify the significance of each selected factor.

3. Results and Discussion

Out of the 435 hourly model runs, 87 valid plume rises were found. The reasons that the rest of the hours were not able to give out a plume rise value are (1) the ∆Cm for that hour was negative, meaning that the measured PM concentration of any possible downwind station was lower than the upwind station; (2) RD> 20%.

3.1. Seasonal Variations of the Plume Rise

Based on the prediction, all plume rises in each season were averaged and compared to see if the seasons would affect the magnitude of the plume rises (Table 4). The plume rises of spring and fall were higher than the other two seasons. In winter time, the average plume rise was much lower than other three seasons. This is probably because in winter times, the ventilation rate was not as high as other seasons. In addition, only 15 valid plume rises were obtained for winter time, among which only three hours were from daytime emissions, the plume rises may be affected by diurnal pattern. The average of these 15 plume rises may not well represent the seasonal mean. For summer time, as the thermal buoyancy was small due to small temperature differences between emission source and ambient air, the main plume rises were mainly due to the ventilation. However, despite the fact that summer had the highest ventilation rate, the plume rise in summer 2009 was not as much as those in fall 2008 and spring 2009. The plume rises for summer times need to be further investigated.

The standard errors in Table 4 show that in spring and fall, the variation of plume rises is the highest. This is probably because of the high variation of house ventilation in response to the fluctuation of in-house temperature. Change of ventilation rate may cause the plume rise to change. On the other hand, in

Table 4. Mean plume rises by seasons.

*Means with different letters are significant at 0.05.

Figure 5. Diurnal variation of the plume rises.

summer and winter, the ventilation rate is relatively stable (either reached maximum ventilation in summer, or stayed at minimum ventilation rate in winter), leading to smaller standard errors for plume rises.

3.2. Diurnal Variation of the Plume Rise

To investigate diurnal variations of the plume rise, the plume rises and the time of a day were sorted together from earlier of the day till the latest ones. The plume rises were then grouped by each two hours from 0:00 to 23:00 and averaged within each group. In results, 12 mean plume rises were obtained and shown in Figure 5. As it can be seen, the lowest plume rise appeared at 2:00-3:00 or 18:00-21:00, the highest plume rise appeared at 8:00-9:00. There was no obvious diurnal impact on the plume rises by sorting the whole set of data. This was probably because that as the weather changed for different seasons, the ventilation varied, thus changing the diurnal patterns. Diurnal results seemed to indicate that the time when the peak plume rise appeared may be a matter of other parameters such as ventilation.

To analyze the response of the plume rises to the house ventilation, both ventilation rates and the plume rises for two representative dates were plotted in Figure 6 & Figure 7. In general, the plume rises responded to the ventilation rates well. The higher the ventilation rate was, the higher the plume rise occurred.

Figure 6. Diurnal variations of the plume rise and ventilation rate on October 11, 2008.

Figure 7. Diurnal variation of the plume rise and ventilation rate on April 16, 2009.

Pearson’s correlation coefficients (ρ) tests were also applied for the two days. For October 11, 2008 (Figure 6), the relationship between ventilation and plume rises is quite firm (ρ = 0.9766) and the diurnal pattern of the plume rise followed very well with the diurnal pattern of the ventilation rate. For April 16, 2009, however, the relationship between the two was very poor (ρ = 0.4391). Although it seems high plume rises occurred at high ventilation rate, the plume rise was abnormally low at 16:00 on April 16, 2009 while the ventilation rate was not. A careful check of all possible related parameters at that hour was conducted for explanation. It was discovered that, except for the ranking of PM10 concentration levels among the four ambient stations, other factors (parameters) were not significantly different from the hourly data before and after this specific hour. At 15:00, 17:00 and even 14:00 of that day, the PM10 concentrations of the ambient stations all followed the order in ST4 > ST2 > ST5 > ST3; while at 16:00 the order was ST2 > ST4 > ST3 > ST5. It is unknown if this change of PM10 concentration ranking among station would have any impact.

3.3. Comparison of the Plume Rises on Weekday versus Weekends

Since the seasonal variation of the plume rises was observed, the comparison of plum rise on weekdays and weekends was conducted within one season. The average plume rises for weekdays and weekends are shown in Table 5.

At a significance level of 0.05, the plume rises during weekends were significantly higher than those during weekdays (p-value = 0.0019) in Fall. For spring, winter and summer, the difference between the two groups was not significant (p-value = 0.1551, 0.4779 and 0.8763, respectively). Comparison of the plume rises for Fall 2008 and Spring 2009 indicates no significant difference between the weekend plume rises for the two seasons, 19.76 m and 24.91 m; but there was a six times’ difference for the weekday plume rises between these two seasons, 2.02 m and 12.78 m. The fact that Winter 2008 and Spring 2009 had the plume rise ratios of Δhweekends/∆hweekdays in 2.02 and 1.95 implies the plume rises for weekends were about twice as much as the plume rises for weekdays.

For those hours providing valid plume rises, the predicted PM10 concentrations by AERMOD for ambient stations were observed to be smaller as the plume rise became larger. This means that if the ambient stations measured greater PM10 concentrations than the true contributions of the farm house emissions only, the inverse-AERMOD would produce smaller plume rise. This may explain the observation that the weekday plume rises tend to be smaller than weekend plume rise since there were some traffics around the farm, contributing PM10 to ambient stations. The PM10 contribution of the farm traffics were included in PM10 measurements at ambient stations and yet not included in emission rate for model simulation.

3.4. Multiple Linear Regression Analysis

To identify the significance of various factors (e.g., wind speed/direction, ambient/ source temperature/RH, solar radiation, ventilation rate) that may affect the plume rise, the linear regression analysis was conducted and results of the analysis are listed in Table 6. The p-values of the multiple linear model shows that the wind speed had the strongest relationship with plume rise (p-value = 0.0134). Wind direction, ambient RH and total volume flow had a little relationship with the plume rises (p-value = 0.2285, 0.1709 and 0.2173, respectively). The possible reason for wind speed to be the most important factor would be the fact that the

Table 5. The impact of weekday and weekend on the plume rises.

Table 6. The multiple linear regression modeling results for the simulated plume rises.

exit velocities for naturally ventilated houses were estimated by the wind speeds, which strengthened the relationship between wind speeds and plume rises. It should also be noticed, the ground temperature could also be a possible factor affecting the plume rise of close to ground level emissions. However, no measurement of the ground temperature was done during the field data collection.

4. Summary and Conclusions

Based on the 87 predictions of plume rises of AERMOD simulations for the selected periods for four seasons, the following findings are obtained:

1) The mean plume rises were 16.2 m (SE = 11.2 m), 7.9 m (SE = 9.5 m), 16.5 m (SE = 12.4 m), 14.3 m (SE = 10.0 m) for fall, winter, spring and summer, respectively. More data are needed to support the prediction, especially for winter times.

2) The relationship between time of a day and the plume rises from animal housing systems did not demonstrate consistent diurnal patterns. However, in general, diurnal patterns of the plume rise followed the patterns of the ventilation rates.

3) The plume rises during weekends were significantly higher than that during weekends.

4) Wind speed had a very strong positive effect on the plume rises, whereas other parameters (i.e., temperature, RH, ventilation, solar radiation and cloud cover) did not show significant impact (p-value > 0.1) on the magnitude of the plume rises.

Acknowledgements

This study was supported in part by NSF CAREER Award No. CBET-0954673 and USDA NIFA Higher Education Challenger Grant Program 2013-70003-20929. The PM source emission data and wind data were monitored under the National Air Emission Monitoring Study (NAEMS) Southeast Layer Operation, which was funded by the American Egg Board. Help from Qianfeng Li on field sampling is also acknowledged.

Conflicts of Interest

The authors declare no conflicts of interest.

Cite this paper

Ying, M. , Wang-Li, L. , Stikeleather, L. and Edwards, J. (2017) Modeling Plume-Rise of Air Emissions from Animal Housing Systems: Inverse AERMOD. Journal of Environmental Protection, 8, 1254-1269. doi: 10.4236/jep.2017.811078.

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