# Baptism of Fire: Modeling the Effects of Prescribed Fire on Lyme Disease

Authors: Emily Guo; Folashade B. Agusto
Journal: Canadian Journal of Infectious Diseases and Medical Microbiology
 (2022)

---

## Abstract

Recently, tick-borne illnesses have been trending upward and are an increasing source of risk to people’s health in the United States. This is due to range expansion in tick habitats as a result of climate change. Thus, it is imperative to find a practical and cost-efficient way of managing tick populations. Prescribed burns are a common form of land management that can be cost-efficient if properly managed and can be applied across large amounts of land. In this study, we present a compartmental model for ticks carrying Lyme disease and uniquely incorporate the effects of prescribed fire using an impulsive system to investigate the effects of prescribed fire intensity (high and low) and the duration between burns. Our study found that fire intensity has a larger impact in reducing tick population than the frequency between burns. Furthermore, burning at high intensity is preferable to burning at low intensity whenever possible, although high-intensity burns may be unrealistic due to environmental factors. Annual burns resulted in the most significant reduction in infectious nymphs, which are the primary carriers of Lyme disease.


---

## Body

## 1. Introduction

Many ticks are disease vectors that significantly impact public health. Reports of overall tick-borne diseases doubled from 2006 to 2018 [1] while the incidence of Lyme disease in the United States has been steadily increasing, from a little less than four cases per 100,000 people in the 1990s to close to 10 cases per 100,000 people in the early 2000s [2]. New pathogens continue to emerge, including heartland virus, Bourbon virus, Borrelia miyamotoi, Borrelia mayonii, and Ehrlichia muris eauclairensis [3]. Climate change has expanded the northern borders of tick habitats and increased winter tick activity, contributing to the prevalence of tick-borne diseases [4]. Therefore, finding a practical and cost-efficient way to manage tick populations has become extremely important. The majority of ticks that carry Lyme disease are infected through mice or other small rodents [5], so most methods that have looked at tick reduction are focused on either host reduction or tick elimination [6]. Ticks can have up to 2- to 3-year long life cycles, with four general stages that each requires one blood meal after the eggs hatch: egg, larvae, nymph, and adult [6]. The majority of human infections come from tick nymphs, which are much smaller than adult ticks (less than 2 mm long or about the size of a poppy seed), making them more difficult to spot on the human body and therefore more likely to remain undetected [6]. Nymphs are also more numerous than adult ticks and are most active during the spring and summer months, when the number of people who spend time outside is substantially larger than those during other months. The black-legged tick, also known as Ixodes scapularis, has a life cycle that generally lasts two years, while the life cycle of the lone star tick (Amblyomma americanum) is around three years long. Most ticks hatch from their eggs in the spring and have the ability to live for three to five months between each blood meal [7].Prescribed fires, or controlled burns, are a common and necessary form of land management in many different environments that are also effective in controlling tick populations. This is through both directly killing ticks along with destroying their leaf litter habitat [7]. Larvae, nymphs, and adults spend the vast majority of their time in leaf litter other than the few days that they are feeding on their hosts. Controlled burns are appealing due to their time and cost efficiency along with their ability to be applied across a large amount of land. They are generally most effective in the late spring and early summer, as that time coincides with when nymph ticks are questing for hosts (although this is heavily dependent on the type of land that is being burned) [8]. Primary concerns around prescribed fire include air quality (due to smoke) and the potential for the fire to burn out of control; however, these can be prevented when proper precautions are taken.Many studies have looked at the impact of prescribed fires on tick populations, with conflicting results. The majority of these studies agree that tick populations decrease immediately after a burn but recover to pre-burn abundance after around one year [6]. Other studies have found that although the nymph population decreased, the risk of encountering infectious nymphs remained the same [9] or that the tick population even increased [10]. However, these studies often fail to account for the logistics of true prescribed burning (long term and over lots of lands on a regular basis) or other predictors of tick abundance such as host abundance, climate, or vegetation structure [6]. There is also the possibility that postburn recolonization rates vary based on tick species, habitat type, climate, and burn intensity [11, 12].A study done by Allan [11] in the oak-hickory ecosystems of the Missouri Ozarks looked at the relationship between lone star tick larval populations and deer abundance under long-term burn management. The sites were burned in the spring at low intensity every 3–5 years. The ticks were depleted but then rapidly grew starting two years postburn, coming back down to pre-burn abundance around five years postburn [11]. The researchers attributed this increase to the high host populations postburn, as freshly burned areas are better for deer to forage in. These issues could be countered by more frequent, longer, and larger-scale burns, which correlate with other studies that also believe that burns at higher intensity are most effective in countering ticks than those at low intensity [13]. Gleim et al. [3] found that long-term prescribed fire (regular burning for 10+ years) significantly reduced tick abundance, regardless of burn interval, host abundance, or vegetation structure. This is primarily due to the change in vegetation structure, creating a hotter and drier environment that is less appealing for ticks [6]. These burnings decreased the encounter rate with infectious ticks by 98% in plots in southwestern Georgia and northwestern Florida. However, more research in a variety of environments needs to be done regarding realistic prescribed burning as a tick management technique.The goal of this study was to develop a compartmental model for ticks carrying Lyme disease to see how they are affected by prescribed burns. Compartmental epidemic models are a modeling technique that segments individuals in the populations into different classes according to individual’s disease status [14]. We look at both fire intensities (high and low) and the duration between fires to understand how this common land practice affects tick populations and the prevalence of Lyme disease among them. We also investigate whether intensity or duration plays a more significant role in tick population reduction overall. To the best of our knowledge, this is the first study to use a mathematical model for Lyme disease to examine the effects of prescribed fire. A preprint of this study has already been published [15].The remainder of the work in this study is organized as follows. In Section2, we formulate our baseline tick/Lyme disease model, compute the model basic reproduction number, and carry out basic stability analysis including sensitivity analysis to determine the parameter with the most impact on the basic reproduction number. In Section 2.3, we describe the tick model with the effect of prescribed fire using an impulsive system of ordinary differential equations and present some stability analysis results of the impulsive system. In Section 2.3.1, we discuss the estimation of parameters related to prescribed fire from literature. In Section 3, we present some simulation results, and in Section 4, we discuss our findings and close with conclusions.


## 2. Materials and Methods

This model was created by incorporating two subgroups: mice and ticks. The mice population is divided into susceptibleSMt and infected mice IMt. The tick population is divided by life stage (eggs, larvae, nymph, and adult) and further divided into susceptible and infected groups for larvae (SLt and ILt), nymphs (SNt and INt), and adults (SAt and IAt). Since ticks must take a blood meal before they become infected and there is no vertical transmission for the disease, all eggs remain susceptible SEt. Individuals move between compartments according to their life stage and disease status. A detailed description of the model formulation is given in Appendix A. The related model schematic is given in Figure 1, and the description of the model variables and parameters is stated in Table 1.Figure 1
Flow diagram of the Lyme disease model for ticks and mice. The mice population is represented by the red boxes and is divided into susceptibleSMt and infected IMt compartments. The tick population is represented by the blue boxes and is divided by life stage and infection status. It consists of susceptible eggs SEt, susceptible larvae SLt, infected larvae ILt, susceptible nymphs SNt, infected nymphs INt, susceptible adults SAt, and infected adults IAt.Table 1
Description of the variables and parameters for the Lyme disease model in Figure1.
VariableDescriptionSMtNumber of susceptible miceIMtNumber of infected miceSEtNumber of eggsSLtNumber of susceptible larvaeILtNumber of infected larvaeSNtNumber of susceptible nymphsINtNumber of infected nymphsSAtNumber of susceptible adultsIAtNumber of infected adultsParameterDescriptionπMMice birth rate0.02[16]μMMice mortality rate0.01[16]βMTick-to-mouse transmission probability0.9[17]πTTick birth rate456.36[16]KCarrying capacity5,000[18]μEDeath rate/inviability rate of the egg0.0025[16]σTEggs to larval developmental rate0.00677[16]μE,μL,μN,μATick mortality rate at different life stagesμTTick mortality rate0.015[16]βTMouse-to-tick transmission probability0.9[17]τTLarvae-to-nymph development rate (or nymph development rate)0.00618[16]γTNymph-to-adult development rate of (adult development rate)0.00491[16]The basic qualitative properties of the tick model shown in Figure1 and described in Appendix A, its positivity, and the boundedness of solutions are given in Appendix B.


### 2.1. Reproduction Numberℛ0

The associated reproduction number, denoted byℛ0, obtained using the next-generation matrix method [19, 20] for the Lyme disease model (A-5) shown in Figure 1 and described in Appendix A, is given as follows:(1)ℛ0=βMβTk1k2SA∗∗+k2μA+τTμA+τTγTSL∗∗+μA+γTk1SN∗∗k1k2μASM∗∗μM.However, we made a simplifying assumption thatμL=μN=μA=μT. Then, the reproduction number in (1) becomes(2)ℛ0=βMβTSA∗+SL∗+SN∗SM∗μMμT.See details in Appendix C.The basic reproduction number,ℛ0, is defined as the expected number of new infections that result from one infectious individual in a population that is fully susceptible [19, 20]. This value is extremely significant because if the reproduction number is less than unity ℛ0≤1 then the disease cannot invade the population and it will die out in the community. Conversely, if ℛ0>1 then the disease will continue to persist in the population. This determines whether there is a possibility of disease elimination or whether the goal should be to manage transmission within the community.


### 2.2. Sensitivity Analysis

Sensitivity analysis was conducted to determine the contribution of each of the model parameters to the reproduction numberℛ0. The results of this help identify which parameters are the best to target regarding interventions and future data collection. A normalized forward sensitivity index was used to determine the ratio of the relative change in ℛ0 based on a relative change in a parameter. The sensitivity indices of ℛ0 are derived as follows:(3)Υpℛ0=∂ℛ0∂p×pℛ0,where Υpℛ0 is the forward sensitivity index of ℛ0 with respect to parameter p. Parameter p is a parameter within ℛ0. The results of this sensitivity analysis are shown in Figure 2.Figure 2
Sensitivity analysis results for the Lyme disease model. The larval development rate, the carrying capacity, and the disease transmission probability for both mice and ticks are all positive influences onℛ0. The mice birth rate and tick death rate are negative influences on ℛ0. Prescribed fire directly increases the tick death rate, making it an effective control strategy.The larval development rate, the carrying capacity of the environment, and the disease transmission probability for both mice and ticks all positively affectℛ0. As these values increase, ℛ0 will also increase. We are more interested in the mice birth rate and the tick death rate, which negatively affect ℛ0. As these parameters decrease, ℛ0 will also decrease. The most influential parameter on ℛ0 is the tick death rate. This suggests that control strategies that effectively target the spread of Lyme disease will focus on increasing the tick death rate and, to a lesser extent, also decreasing the mice birth rate. The sensitivity analysis aligns with our results from the model, as prescribed fire is a mechanism that most significantly affects the tick death rate.


### 2.3. Tick Model with Prescribed Fire

In this section, we consider the effect of fire on ticks and the small mammal population. We do not explicitly incorporate fire into the model shown in Figure1 and described in Appendix A; rather, we consider the effect of fire on population size after the burns. To introduce the effect of prescribed fire into the Lyme disease model, we have the following system of nonautonomous impulsive differential equations.(4)dSMdt=πM−λMSM−μMSMdIMdt=λMSM−μMIMdSEdt=πT1−SEKSA+IA−σT+μESEdSLdt=σTSE−λTSL−τT+μLSLdILdt=λTSL−τT+μLILdSNdt=τTSL−λTSN−γT+μNSNdINdt=τTIL+λTSN−γT+μNINdSAdt=γTSN−λTSA−μASAdIAdt=γTIN+λTSA−μAIAt≠nT,n∈ℕ.Subject to the prescribed fire impulsive condition:(5)SMnT+=1−νMSMnT−IMnT+=1−νMlMnT−SEnT+=1−νESEnT−SLnT+=1−νLSLnT−ILnT+=1−νLSLnT−SNnT+=1−νNSNnT−INnT+=1−νNINnT−SAnT+=1−νASAnT−IAnT+=1−νAIAnT−t=nT,n∈ℕ,where tn is the times that prescribed fire is implemented, which may be fixed or non-fixed; within this study, we will consider the case with fixed times. The parameters νj,wherej=E,L,N,A,M are the proportion of the tick and mice population that is reduced by the fire. In Section 2.3.1, we discuss how these parameters are estimated using data from low- and high-intensity fires. The existence and stability of the impulsive model (3) are given in Appendix D.


#### 2.3.1. Prescribed Fire Parameter Estimation

To estimate the parametersνL,νN,νA,νM that quantify the reduction in each tick life stage and mice population after the different burn intensities (low and high burns), we use data from [13, 21]. The parameters for each life stage relating to the low-intensity burn were estimated using data from [13], while the parameters relating to the high-intensity burn were estimated using data from [21]. Each group of parameters was separated into the larval, nymph, and adult life stages, but only data in [21] provided data to estimate the parameter for mice population. Below, we give a summary description of the study sites in each study, the amount of ticks and mice collected, and how these parameters are estimated from the data collected.(1) High-Intensity Fire. The study in [21] was conducted in chaparral habitat at the University of California, Hopland Research and Extension Center, in Mendocino County, CA. The study took advantage of two prescribed fires ignited on June 1, 1995, that were intended to reduce fire load in two chaparral plots, Maude’s Glade (MG) and Don’s Brush Plot (DBP). The fires were ignited by hand crews using drip torches in a strip headfire configuration to produce relatively uniform fire behavior that left no live branches in the shrub line, which we assume as high-intensity fire. For a period of 13 months beginning a month before the burn, control and treatment areas were monitored for the presence of ticks by flagging the vegetation or ground between 0800 and 1000 hours. Each flag sample involved sweeping a standard 1 m2 white flannel tick flag in a 180° arc from a particular bush. The number of flag samples varied between 24 and 184 samples per day per plot. Ticks collected from these flag samples had their species and sex recorded and then that were released at the site of capture. Carbon dioxide (CO2) trapping was done monthly, starting one month before the burn, and ending one year after the burn date. Ten enamelware pans were buried at 15 m intervals as pitfall traps. 5–10 g of dry ice was added to the center of the pan between 1000 and 1200 hours at control sites and between 1200 and 1400 hours at treatment sites. Ticks were collected 2 hours after the addition of dry ice and had their numbers, species, sex, and life stage recorded and then that were released at the site of capture. To assess the abundance of rodents and the associated ticks on them, live traps were set to catch the rodents. Non-folding Sherman traps were set at 7.5 m intervals along the ecotones of the area, starting one week before the burn and continuing for two simultaneous nights each month throughout the duration of the study.At the two study sites (MG and DBP), six tick species (namelyIxodes pacificus, Ixodes jellisoni, Ixodes spinipalpis, Ixodes woodi, Dermacentor occidentalis, and Dermacentor parumapertus) were removed from the six different rodents species caught; these include California kangaroo rat (Dipodomys californicus californicus), brush mouse (Peromyscus boylii), pinyon mouse (P. truei sequoiensis), deer mouse (P. maniculatus gambelii), dusky-footed woodrat (Neotoma fuscipes), and western harvest mouse (Reithrodontomys megalotis longicaudus). After the fire treatment, about half as many rodents were trapped at the treated sites compared with control sites.All the ixodid tick species (Ixodes pacificus, Ixodes jellisoni, Ixodes spinipalpis, Ixodes woodi) are competent hosts that are able to transmit Lyme disease, but we use only the data of Ixodes pacificus to estimate the parameter used to quantify the reduction in the tick population as a result of fire. Table 2 gives a breakdown of Ixodes pacificus collected on the rodents in the control and treated areas at both MG and DBP sites, as well as the number of rodents collected at these sites pre- and postburn.Table 2
Data taken from [21] under assumed high-intensity fire. C = control and B = burn.
LarvaeCLarvaeBNymphCNymphBAdultCAdultBRodentCRodentBDBP79101311455627MG801702875425Total15911833221211052(2) Computing Parameters. νL,νN,νA,νMfor High-Intensity Fire. To compute these parameters, we assume that equal numbers of ticks and rodents are in the sites (control and treated sites) pre-burn, and the difference in number is due to the burn, since we have no way to measure exactly the number of ticks in all the study sites. First, we take the difference between the total number of ticks and mice in the control and treatment sites and divide it by the total number of ticks and mice in the control sites. Then, we subtract these proportions from 1 to give the proportions reduced as a result of the burn:(6)adult:22−12184=0.05435,⇒νA=1−0.05435=0.5454,nymphs:3−33=0184=0.0,⇒νN=1−0=1,larvae:159−118184=0.2228,⇒νL=1−0.2228=0.7421,mice:110−52110=0.5272⇒νM=1−0.5272=0.4728.(3) Low-Intensity Fire. The study in [13] was conducted in an open oak woodland barren complex at Western Illinois University’s Alice L. Kibbe Field Station located in Warsaw, in Hancock County, IL, USA. These areas are comprised of multiple habitat types including oak-hickory woodlands, early successional woodlands, oak barrens, floodplain forests, restored tallgrass prairies, and hill prairies. The entire study site was last burned in 2004 (B04), and two additional burns were carried out in spring of 2014 (B14) and 2015 (B15). The burns were considered low intensity because most flame heights were less than 1 meter and plant mortality was limited to the understory vegetative community [22].Ticks were collected through a flagging method similar to that of the high-intensity fire, where a 1 m2 flannel cloth was attached to a dowel (although they used bamboo instead of wood) and swept through the vegetation. This was done every two weeks when the vegetation was dry between 1200 and 1800 hours during two consecutive years (May 9, 2015, to October 30, 2015, and April 22, 2016, to November 4, 2016). The cloth flag was then placed into a sealed bag and frozen for three days to ensure tick mortality. The ticks were removed and identified using taxonomic keys; ticks collected in 2015 and 2016 also had their DNA extracted. A total of 2788 Amblyomma americanum, 54 Ixodes scapularis, and 23 Dermacentor variabilis ticks were collected in 2015 and 2016. Amblyomma americanum ticks collected in B04 made up 51% of the collection n=1433, while those collected in B14 made up 37% n=1045 of the collections, and those collected in B15 constituted 11% n=307 of the collection. Of these ticks, 2% n=67 were adults, 4% n=107 were nymphs, and 93% n=2614 were larvae. Of the 23 D. variabilis collected, 74% n=17 were adults, 9% n=2 were nymphs, and 17% n=4 were larvae, while 4% n=2 of the 54 I. scapularis collected were adults, 22% n=12 were nymphs, and 74% n=40 were larvae. Here, we use the data collected for Ixodes scapularis to estimate the parameter quantifying the reduction in the tick population due to fire since I. scapularis can transmit Lyme disease. The study did not indicate whether these were data for the pre-burn or postburn number of I. scapularis collected, nor did it provide data for the number of mice that were caught.(4) Estimating Parameters. νL,νN,νA,νMfor Low-Intensity Fire. To estimate these parameters, we assume that the 54 I. scapularis collected are the ticks left after the burn. We then divide the numbers collected in each age group by the total number collected and subtract the proportion obtained from 1 to obtain the proportion reduced by fire.(7)adult:254=0.037,⇒νA=1−0.037=0.9629,nymphs:1254=0.222,⇒νN=1−0.222=0.7778,larvae:4054=0.741,⇒νL=1−0.741=0.2593.Although these were the best sources of data we could find (that accounted for tick life stages pre- and postburn along with fire intensity), unfortunately, they were not ideal. The burns were conducted in vastly different environments—the high-intensity fire took place in California chaparral, while the low-intensity fire took place in Illinois oak woodland. The high-intensity burn was only conducted once in the summer, while the low-intensity burn was conducted in the spring for two consecutive years. We were unable to find any sources of data from similar geographic locations or number of burns that were detailed enough in terms of tick data and fire intensity data to be used. These variances between the two data sets have the potential to drastically affect the burn results.


## 2.1. Reproduction Numberℛ0

The associated reproduction number, denoted byℛ0, obtained using the next-generation matrix method [19, 20] for the Lyme disease model (A-5) shown in Figure 1 and described in Appendix A, is given as follows:(1)ℛ0=βMβTk1k2SA∗∗+k2μA+τTμA+τTγTSL∗∗+μA+γTk1SN∗∗k1k2μASM∗∗μM.However, we made a simplifying assumption thatμL=μN=μA=μT. Then, the reproduction number in (1) becomes(2)ℛ0=βMβTSA∗+SL∗+SN∗SM∗μMμT.See details in Appendix C.The basic reproduction number,ℛ0, is defined as the expected number of new infections that result from one infectious individual in a population that is fully susceptible [19, 20]. This value is extremely significant because if the reproduction number is less than unity ℛ0≤1 then the disease cannot invade the population and it will die out in the community. Conversely, if ℛ0>1 then the disease will continue to persist in the population. This determines whether there is a possibility of disease elimination or whether the goal should be to manage transmission within the community.


## 2.2. Sensitivity Analysis

Sensitivity analysis was conducted to determine the contribution of each of the model parameters to the reproduction numberℛ0. The results of this help identify which parameters are the best to target regarding interventions and future data collection. A normalized forward sensitivity index was used to determine the ratio of the relative change in ℛ0 based on a relative change in a parameter. The sensitivity indices of ℛ0 are derived as follows:(3)Υpℛ0=∂ℛ0∂p×pℛ0,where Υpℛ0 is the forward sensitivity index of ℛ0 with respect to parameter p. Parameter p is a parameter within ℛ0. The results of this sensitivity analysis are shown in Figure 2.Figure 2
Sensitivity analysis results for the Lyme disease model. The larval development rate, the carrying capacity, and the disease transmission probability for both mice and ticks are all positive influences onℛ0. The mice birth rate and tick death rate are negative influences on ℛ0. Prescribed fire directly increases the tick death rate, making it an effective control strategy.The larval development rate, the carrying capacity of the environment, and the disease transmission probability for both mice and ticks all positively affectℛ0. As these values increase, ℛ0 will also increase. We are more interested in the mice birth rate and the tick death rate, which negatively affect ℛ0. As these parameters decrease, ℛ0 will also decrease. The most influential parameter on ℛ0 is the tick death rate. This suggests that control strategies that effectively target the spread of Lyme disease will focus on increasing the tick death rate and, to a lesser extent, also decreasing the mice birth rate. The sensitivity analysis aligns with our results from the model, as prescribed fire is a mechanism that most significantly affects the tick death rate.


## 2.3. Tick Model with Prescribed Fire

In this section, we consider the effect of fire on ticks and the small mammal population. We do not explicitly incorporate fire into the model shown in Figure1 and described in Appendix A; rather, we consider the effect of fire on population size after the burns. To introduce the effect of prescribed fire into the Lyme disease model, we have the following system of nonautonomous impulsive differential equations.(4)dSMdt=πM−λMSM−μMSMdIMdt=λMSM−μMIMdSEdt=πT1−SEKSA+IA−σT+μESEdSLdt=σTSE−λTSL−τT+μLSLdILdt=λTSL−τT+μLILdSNdt=τTSL−λTSN−γT+μNSNdINdt=τTIL+λTSN−γT+μNINdSAdt=γTSN−λTSA−μASAdIAdt=γTIN+λTSA−μAIAt≠nT,n∈ℕ.Subject to the prescribed fire impulsive condition:(5)SMnT+=1−νMSMnT−IMnT+=1−νMlMnT−SEnT+=1−νESEnT−SLnT+=1−νLSLnT−ILnT+=1−νLSLnT−SNnT+=1−νNSNnT−INnT+=1−νNINnT−SAnT+=1−νASAnT−IAnT+=1−νAIAnT−t=nT,n∈ℕ,where tn is the times that prescribed fire is implemented, which may be fixed or non-fixed; within this study, we will consider the case with fixed times. The parameters νj,wherej=E,L,N,A,M are the proportion of the tick and mice population that is reduced by the fire. In Section 2.3.1, we discuss how these parameters are estimated using data from low- and high-intensity fires. The existence and stability of the impulsive model (3) are given in Appendix D.


### 2.3.1. Prescribed Fire Parameter Estimation

To estimate the parametersνL,νN,νA,νM that quantify the reduction in each tick life stage and mice population after the different burn intensities (low and high burns), we use data from [13, 21]. The parameters for each life stage relating to the low-intensity burn were estimated using data from [13], while the parameters relating to the high-intensity burn were estimated using data from [21]. Each group of parameters was separated into the larval, nymph, and adult life stages, but only data in [21] provided data to estimate the parameter for mice population. Below, we give a summary description of the study sites in each study, the amount of ticks and mice collected, and how these parameters are estimated from the data collected.(1) High-Intensity Fire. The study in [21] was conducted in chaparral habitat at the University of California, Hopland Research and Extension Center, in Mendocino County, CA. The study took advantage of two prescribed fires ignited on June 1, 1995, that were intended to reduce fire load in two chaparral plots, Maude’s Glade (MG) and Don’s Brush Plot (DBP). The fires were ignited by hand crews using drip torches in a strip headfire configuration to produce relatively uniform fire behavior that left no live branches in the shrub line, which we assume as high-intensity fire. For a period of 13 months beginning a month before the burn, control and treatment areas were monitored for the presence of ticks by flagging the vegetation or ground between 0800 and 1000 hours. Each flag sample involved sweeping a standard 1 m2 white flannel tick flag in a 180° arc from a particular bush. The number of flag samples varied between 24 and 184 samples per day per plot. Ticks collected from these flag samples had their species and sex recorded and then that were released at the site of capture. Carbon dioxide (CO2) trapping was done monthly, starting one month before the burn, and ending one year after the burn date. Ten enamelware pans were buried at 15 m intervals as pitfall traps. 5–10 g of dry ice was added to the center of the pan between 1000 and 1200 hours at control sites and between 1200 and 1400 hours at treatment sites. Ticks were collected 2 hours after the addition of dry ice and had their numbers, species, sex, and life stage recorded and then that were released at the site of capture. To assess the abundance of rodents and the associated ticks on them, live traps were set to catch the rodents. Non-folding Sherman traps were set at 7.5 m intervals along the ecotones of the area, starting one week before the burn and continuing for two simultaneous nights each month throughout the duration of the study.At the two study sites (MG and DBP), six tick species (namelyIxodes pacificus, Ixodes jellisoni, Ixodes spinipalpis, Ixodes woodi, Dermacentor occidentalis, and Dermacentor parumapertus) were removed from the six different rodents species caught; these include California kangaroo rat (Dipodomys californicus californicus), brush mouse (Peromyscus boylii), pinyon mouse (P. truei sequoiensis), deer mouse (P. maniculatus gambelii), dusky-footed woodrat (Neotoma fuscipes), and western harvest mouse (Reithrodontomys megalotis longicaudus). After the fire treatment, about half as many rodents were trapped at the treated sites compared with control sites.All the ixodid tick species (Ixodes pacificus, Ixodes jellisoni, Ixodes spinipalpis, Ixodes woodi) are competent hosts that are able to transmit Lyme disease, but we use only the data of Ixodes pacificus to estimate the parameter used to quantify the reduction in the tick population as a result of fire. Table 2 gives a breakdown of Ixodes pacificus collected on the rodents in the control and treated areas at both MG and DBP sites, as well as the number of rodents collected at these sites pre- and postburn.Table 2
Data taken from [21] under assumed high-intensity fire. C = control and B = burn.
LarvaeCLarvaeBNymphCNymphBAdultCAdultBRodentCRodentBDBP79101311455627MG801702875425Total15911833221211052(2) Computing Parameters. νL,νN,νA,νMfor High-Intensity Fire. To compute these parameters, we assume that equal numbers of ticks and rodents are in the sites (control and treated sites) pre-burn, and the difference in number is due to the burn, since we have no way to measure exactly the number of ticks in all the study sites. First, we take the difference between the total number of ticks and mice in the control and treatment sites and divide it by the total number of ticks and mice in the control sites. Then, we subtract these proportions from 1 to give the proportions reduced as a result of the burn:(6)adult:22−12184=0.05435,⇒νA=1−0.05435=0.5454,nymphs:3−33=0184=0.0,⇒νN=1−0=1,larvae:159−118184=0.2228,⇒νL=1−0.2228=0.7421,mice:110−52110=0.5272⇒νM=1−0.5272=0.4728.(3) Low-Intensity Fire. The study in [13] was conducted in an open oak woodland barren complex at Western Illinois University’s Alice L. Kibbe Field Station located in Warsaw, in Hancock County, IL, USA. These areas are comprised of multiple habitat types including oak-hickory woodlands, early successional woodlands, oak barrens, floodplain forests, restored tallgrass prairies, and hill prairies. The entire study site was last burned in 2004 (B04), and two additional burns were carried out in spring of 2014 (B14) and 2015 (B15). The burns were considered low intensity because most flame heights were less than 1 meter and plant mortality was limited to the understory vegetative community [22].Ticks were collected through a flagging method similar to that of the high-intensity fire, where a 1 m2 flannel cloth was attached to a dowel (although they used bamboo instead of wood) and swept through the vegetation. This was done every two weeks when the vegetation was dry between 1200 and 1800 hours during two consecutive years (May 9, 2015, to October 30, 2015, and April 22, 2016, to November 4, 2016). The cloth flag was then placed into a sealed bag and frozen for three days to ensure tick mortality. The ticks were removed and identified using taxonomic keys; ticks collected in 2015 and 2016 also had their DNA extracted. A total of 2788 Amblyomma americanum, 54 Ixodes scapularis, and 23 Dermacentor variabilis ticks were collected in 2015 and 2016. Amblyomma americanum ticks collected in B04 made up 51% of the collection n=1433, while those collected in B14 made up 37% n=1045 of the collections, and those collected in B15 constituted 11% n=307 of the collection. Of these ticks, 2% n=67 were adults, 4% n=107 were nymphs, and 93% n=2614 were larvae. Of the 23 D. variabilis collected, 74% n=17 were adults, 9% n=2 were nymphs, and 17% n=4 were larvae, while 4% n=2 of the 54 I. scapularis collected were adults, 22% n=12 were nymphs, and 74% n=40 were larvae. Here, we use the data collected for Ixodes scapularis to estimate the parameter quantifying the reduction in the tick population due to fire since I. scapularis can transmit Lyme disease. The study did not indicate whether these were data for the pre-burn or postburn number of I. scapularis collected, nor did it provide data for the number of mice that were caught.(4) Estimating Parameters. νL,νN,νA,νMfor Low-Intensity Fire. To estimate these parameters, we assume that the 54 I. scapularis collected are the ticks left after the burn. We then divide the numbers collected in each age group by the total number collected and subtract the proportion obtained from 1 to obtain the proportion reduced by fire.(7)adult:254=0.037,⇒νA=1−0.037=0.9629,nymphs:1254=0.222,⇒νN=1−0.222=0.7778,larvae:4054=0.741,⇒νL=1−0.741=0.2593.Although these were the best sources of data we could find (that accounted for tick life stages pre- and postburn along with fire intensity), unfortunately, they were not ideal. The burns were conducted in vastly different environments—the high-intensity fire took place in California chaparral, while the low-intensity fire took place in Illinois oak woodland. The high-intensity burn was only conducted once in the summer, while the low-intensity burn was conducted in the spring for two consecutive years. We were unable to find any sources of data from similar geographic locations or number of burns that were detailed enough in terms of tick data and fire intensity data to be used. These variances between the two data sets have the potential to drastically affect the burn results.


## 2.3.1. Prescribed Fire Parameter Estimation

To estimate the parametersνL,νN,νA,νM that quantify the reduction in each tick life stage and mice population after the different burn intensities (low and high burns), we use data from [13, 21]. The parameters for each life stage relating to the low-intensity burn were estimated using data from [13], while the parameters relating to the high-intensity burn were estimated using data from [21]. Each group of parameters was separated into the larval, nymph, and adult life stages, but only data in [21] provided data to estimate the parameter for mice population. Below, we give a summary description of the study sites in each study, the amount of ticks and mice collected, and how these parameters are estimated from the data collected.(1) High-Intensity Fire. The study in [21] was conducted in chaparral habitat at the University of California, Hopland Research and Extension Center, in Mendocino County, CA. The study took advantage of two prescribed fires ignited on June 1, 1995, that were intended to reduce fire load in two chaparral plots, Maude’s Glade (MG) and Don’s Brush Plot (DBP). The fires were ignited by hand crews using drip torches in a strip headfire configuration to produce relatively uniform fire behavior that left no live branches in the shrub line, which we assume as high-intensity fire. For a period of 13 months beginning a month before the burn, control and treatment areas were monitored for the presence of ticks by flagging the vegetation or ground between 0800 and 1000 hours. Each flag sample involved sweeping a standard 1 m2 white flannel tick flag in a 180° arc from a particular bush. The number of flag samples varied between 24 and 184 samples per day per plot. Ticks collected from these flag samples had their species and sex recorded and then that were released at the site of capture. Carbon dioxide (CO2) trapping was done monthly, starting one month before the burn, and ending one year after the burn date. Ten enamelware pans were buried at 15 m intervals as pitfall traps. 5–10 g of dry ice was added to the center of the pan between 1000 and 1200 hours at control sites and between 1200 and 1400 hours at treatment sites. Ticks were collected 2 hours after the addition of dry ice and had their numbers, species, sex, and life stage recorded and then that were released at the site of capture. To assess the abundance of rodents and the associated ticks on them, live traps were set to catch the rodents. Non-folding Sherman traps were set at 7.5 m intervals along the ecotones of the area, starting one week before the burn and continuing for two simultaneous nights each month throughout the duration of the study.At the two study sites (MG and DBP), six tick species (namelyIxodes pacificus, Ixodes jellisoni, Ixodes spinipalpis, Ixodes woodi, Dermacentor occidentalis, and Dermacentor parumapertus) were removed from the six different rodents species caught; these include California kangaroo rat (Dipodomys californicus californicus), brush mouse (Peromyscus boylii), pinyon mouse (P. truei sequoiensis), deer mouse (P. maniculatus gambelii), dusky-footed woodrat (Neotoma fuscipes), and western harvest mouse (Reithrodontomys megalotis longicaudus). After the fire treatment, about half as many rodents were trapped at the treated sites compared with control sites.All the ixodid tick species (Ixodes pacificus, Ixodes jellisoni, Ixodes spinipalpis, Ixodes woodi) are competent hosts that are able to transmit Lyme disease, but we use only the data of Ixodes pacificus to estimate the parameter used to quantify the reduction in the tick population as a result of fire. Table 2 gives a breakdown of Ixodes pacificus collected on the rodents in the control and treated areas at both MG and DBP sites, as well as the number of rodents collected at these sites pre- and postburn.Table 2
Data taken from [21] under assumed high-intensity fire. C = control and B = burn.
LarvaeCLarvaeBNymphCNymphBAdultCAdultBRodentCRodentBDBP79101311455627MG801702875425Total15911833221211052(2) Computing Parameters. νL,νN,νA,νMfor High-Intensity Fire. To compute these parameters, we assume that equal numbers of ticks and rodents are in the sites (control and treated sites) pre-burn, and the difference in number is due to the burn, since we have no way to measure exactly the number of ticks in all the study sites. First, we take the difference between the total number of ticks and mice in the control and treatment sites and divide it by the total number of ticks and mice in the control sites. Then, we subtract these proportions from 1 to give the proportions reduced as a result of the burn:(6)adult:22−12184=0.05435,⇒νA=1−0.05435=0.5454,nymphs:3−33=0184=0.0,⇒νN=1−0=1,larvae:159−118184=0.2228,⇒νL=1−0.2228=0.7421,mice:110−52110=0.5272⇒νM=1−0.5272=0.4728.(3) Low-Intensity Fire. The study in [13] was conducted in an open oak woodland barren complex at Western Illinois University’s Alice L. Kibbe Field Station located in Warsaw, in Hancock County, IL, USA. These areas are comprised of multiple habitat types including oak-hickory woodlands, early successional woodlands, oak barrens, floodplain forests, restored tallgrass prairies, and hill prairies. The entire study site was last burned in 2004 (B04), and two additional burns were carried out in spring of 2014 (B14) and 2015 (B15). The burns were considered low intensity because most flame heights were less than 1 meter and plant mortality was limited to the understory vegetative community [22].Ticks were collected through a flagging method similar to that of the high-intensity fire, where a 1 m2 flannel cloth was attached to a dowel (although they used bamboo instead of wood) and swept through the vegetation. This was done every two weeks when the vegetation was dry between 1200 and 1800 hours during two consecutive years (May 9, 2015, to October 30, 2015, and April 22, 2016, to November 4, 2016). The cloth flag was then placed into a sealed bag and frozen for three days to ensure tick mortality. The ticks were removed and identified using taxonomic keys; ticks collected in 2015 and 2016 also had their DNA extracted. A total of 2788 Amblyomma americanum, 54 Ixodes scapularis, and 23 Dermacentor variabilis ticks were collected in 2015 and 2016. Amblyomma americanum ticks collected in B04 made up 51% of the collection n=1433, while those collected in B14 made up 37% n=1045 of the collections, and those collected in B15 constituted 11% n=307 of the collection. Of these ticks, 2% n=67 were adults, 4% n=107 were nymphs, and 93% n=2614 were larvae. Of the 23 D. variabilis collected, 74% n=17 were adults, 9% n=2 were nymphs, and 17% n=4 were larvae, while 4% n=2 of the 54 I. scapularis collected were adults, 22% n=12 were nymphs, and 74% n=40 were larvae. Here, we use the data collected for Ixodes scapularis to estimate the parameter quantifying the reduction in the tick population due to fire since I. scapularis can transmit Lyme disease. The study did not indicate whether these were data for the pre-burn or postburn number of I. scapularis collected, nor did it provide data for the number of mice that were caught.(4) Estimating Parameters. νL,νN,νA,νMfor Low-Intensity Fire. To estimate these parameters, we assume that the 54 I. scapularis collected are the ticks left after the burn. We then divide the numbers collected in each age group by the total number collected and subtract the proportion obtained from 1 to obtain the proportion reduced by fire.(7)adult:254=0.037,⇒νA=1−0.037=0.9629,nymphs:1254=0.222,⇒νN=1−0.222=0.7778,larvae:4054=0.741,⇒νL=1−0.741=0.2593.Although these were the best sources of data we could find (that accounted for tick life stages pre- and postburn along with fire intensity), unfortunately, they were not ideal. The burns were conducted in vastly different environments—the high-intensity fire took place in California chaparral, while the low-intensity fire took place in Illinois oak woodland. The high-intensity burn was only conducted once in the summer, while the low-intensity burn was conducted in the spring for two consecutive years. We were unable to find any sources of data from similar geographic locations or number of burns that were detailed enough in terms of tick data and fire intensity data to be used. These variances between the two data sets have the potential to drastically affect the burn results.


## 3. Results

To address our research goals, we started by looking at how different burn frequencies and intensities affected tick populations, focusing specifically on the nymphs, since the primary mode of transmission for Lyme disease from ticks to humans is through infectious nymphs. High-intensity fires substantially change the aboveground structure, with no live branches and few shrub skeletons leftover [12, 22]. These burns are much more uniform than those at lower intensities, which are patchy and have vegetation cover and woody debris leftover that ticks are able to survive the burn-in [13]. Our first simulation in Figure 3 shows the substantial difference between high-intensity and low-intensity burns regarding how effective they are at reducing the infectious nymph population. Although both burns start out at around the same effectiveness regardless of intensity, the high-intensity burn proves to reduce the infectious nymph population much more efficiently than the low-intensity burn. The infectious nymph population affected by the low-intensity fire continues to increase despite the burns, while the infectious nymph population affected by the high-intensity fire remains consistently low.Figure 3
Simulation of annual burns for six years at varying intensities. Parameter values are given in Table1.In our second simulation shown in Figure4, we consider the duration between burns for both high- and low-intensity fires. We consider the effects of burning for a period of six years once every six years, once every three years, once every other year, and annually. We found in general that as the duration between burns decreases the infectious nymph population also decreases regardless of the burn intensities. Furthermore, we found that the duration between burns has a more significant effect on ticks with higher-intensity fires than with lower-intensity fires. Fire intensity appears to have a larger influence on tick reduction than the duration of the burns, as burning fewer times at a higher intensity is more effective than burning more times at a lower intensity. For example, high-intensity burns once every three years reduce the infectious nymph population more than low-intensity burns once every two years. However, high-intensity burns might be unrealistic due to environmental factors. In that case, annual burns at low intensity result in the most significant reduction in infectious nymphs in its category.Figure 4
Simulation of varying intervals between burns, separated by their intensity.


## 4. Discussion and Conclusions

### 4.1. Discussion

The most effective simulation in minimizing infectious nymph populations is having annual high-intensity burns, although this is not always practical due to environmental factors such as weather, burn location, and fuel loads. The geographic location of the burn is also important to consider, as it is riskier to have higher-intensity fires closer to human settlements. Most prescribed fires are at low to moderate intensity and are repeated every 1–5 years, with their primary objective being to reduce fuel loads and act as a wildfire prevention tool [21]. There have been a few negative outcomes associated with intense annual burning such as oak tree mortality, soil compaction, and an increased number of tree cankers and tree colonization by root fungus [23], but these depend heavily on the type of environment that is being burned. Overall, infectious tick populations substantially decrease as the time between burns also decreases, regardless of the intensity that the burn is conducted at.These findings were confirmed in a private conversation with Gallagher of the U.S. Forest Service Research and Development team. He recently finished working on a study that looked at how long-term prescribed burns affected tick populations in New Jersey oak woodlands. They found preliminary data that strongly suggest that different tick species are impacted differently by prescribed burns due to their varying moisture sensitivities [12]. It appears that black-legged ticks, the primary vector of Lyme disease in humans, are the most sensitive to moisture loss, while Lone Star ticks and Gulf Coast ticks seem to be more resilient. Gallagher believes that one of the reasons for this is the thickness of the scutum, which is a shield-like plate on the back of hardback ticks [12]. In general, initial data from this study agree with the results of our model. Their high-intensity burns, occurring once every 20 years with data collection for four consecutive years after the burn, saw the greatest reduction in tick populations. Annual low-intensity burns for over 25 years had the second largest tick reduction, while the single low-intensity burn showed the smallest amount of tick reduction.Few research studies have examined the effects of prescribed fire on tick populations and disease prevalence [11]. The studies do often choose to focus on one aspect, usually that of how the burns affect the ticks, with the fire itself being of secondary interest [7]. Future research that records detailed information about fires, such as flame height, difference in vegetation presence before and after the burn, how the fire was ignited, weather conditions during the burns, and overall fire behavior, would be extremely helpful in ensuring the accuracy of the parameters used in the model. Knowledge about the exact dates of the burns and the specifics of the duration between burns is also useful, as seasonality has the potential to play a large role in the effectiveness of burns on disease prevalence. This is especially true with diseases that are primarily found to be transmitted to humans in a certain life stage of the tick, such as with nymphs and Lyme disease. Knowing the exact dates of the burns along with the time in between is useful when comparing the burn results to tick life cycles. For example, spring burns will mostly kill nymphs, although this can vary by species. Noting the geographic context is also important, as the environment plays a role in how these burn impact tick populations. Finally, increasing the time frame of studies that look at how prescribed fire impacts ticks will also be useful. Many studies that claim to study how ticks are affected by prescribed fires only involve a single burn, which is vastly different from true prescribed burning, which involves regular fires over many years.Land geography seems to have a role in the effectiveness of prescribed burns on tick population reduction regarding how fast the environment is able to regrow back to its original state before the burn, although to the best of our knowledge there have not been any studies that specifically look at this. Certain environmental factors might make certain geographic locations better candidates for prescribed fires when the main goal is to reduce tick populations, and this is a subject that is worth looking into in the future. It also appears that different tick species have different levels of heat and moisture resistance, causing them to be affected differently by the fires [12, 13]. Only very preliminary research has been done on this so far, although it is a topic that will substantially influence the choice of whether or not to use prescribed fires for tick reduction.


### 4.2. Conclusion

To conclude, in this study we develop a simple model for Lyme disease transmission and used it to investigate the impact of prescribed burn frequency and fire intensity on the spread of Lyme disease. To the best of our knowledge, this is the first model to incorporate the effect of fire into a mathematical model of ticks and Lyme disease. The key findings from this study are summarized as follows.The simulations of the Lyme disease model (A-5) with prescribed burns show that the following:(i)
The most influential parameters impacting the reproduction number,ℛ0, from the sensitivity analysis are πM,σT,K,μT,βT,βM.(ii)
Intensity appears to be a larger influence on tick reduction than duration is—it is better to burn fewer times at a high intensity than to burn more often at a lower intensity.(iii)
Burning at high intensity is preferable to burning at low intensity whenever possible, although the high intensity may be unrealistic due to environmental factors.(iv)
For low intensity, annual burns resulted in the most significant reduction in infectious nymphs, which are the primary carriers of Lyme disease.This study has shown the effect of prescribed fire on ticks and the spread of Lyme disease. In a future study, we will consider the impact of seasonality on the effectiveness of prescribed burns and the impact of the timing of the burns on disease spread. Geographic landscape and tick habitat are important factors affecting the tick population. In another future work, we will consider different types of geographic landscapes and determine which landscape is most effective in using prescribed burns for tick population control and reduction.


## 4.1. Discussion

The most effective simulation in minimizing infectious nymph populations is having annual high-intensity burns, although this is not always practical due to environmental factors such as weather, burn location, and fuel loads. The geographic location of the burn is also important to consider, as it is riskier to have higher-intensity fires closer to human settlements. Most prescribed fires are at low to moderate intensity and are repeated every 1–5 years, with their primary objective being to reduce fuel loads and act as a wildfire prevention tool [21]. There have been a few negative outcomes associated with intense annual burning such as oak tree mortality, soil compaction, and an increased number of tree cankers and tree colonization by root fungus [23], but these depend heavily on the type of environment that is being burned. Overall, infectious tick populations substantially decrease as the time between burns also decreases, regardless of the intensity that the burn is conducted at.These findings were confirmed in a private conversation with Gallagher of the U.S. Forest Service Research and Development team. He recently finished working on a study that looked at how long-term prescribed burns affected tick populations in New Jersey oak woodlands. They found preliminary data that strongly suggest that different tick species are impacted differently by prescribed burns due to their varying moisture sensitivities [12]. It appears that black-legged ticks, the primary vector of Lyme disease in humans, are the most sensitive to moisture loss, while Lone Star ticks and Gulf Coast ticks seem to be more resilient. Gallagher believes that one of the reasons for this is the thickness of the scutum, which is a shield-like plate on the back of hardback ticks [12]. In general, initial data from this study agree with the results of our model. Their high-intensity burns, occurring once every 20 years with data collection for four consecutive years after the burn, saw the greatest reduction in tick populations. Annual low-intensity burns for over 25 years had the second largest tick reduction, while the single low-intensity burn showed the smallest amount of tick reduction.Few research studies have examined the effects of prescribed fire on tick populations and disease prevalence [11]. The studies do often choose to focus on one aspect, usually that of how the burns affect the ticks, with the fire itself being of secondary interest [7]. Future research that records detailed information about fires, such as flame height, difference in vegetation presence before and after the burn, how the fire was ignited, weather conditions during the burns, and overall fire behavior, would be extremely helpful in ensuring the accuracy of the parameters used in the model. Knowledge about the exact dates of the burns and the specifics of the duration between burns is also useful, as seasonality has the potential to play a large role in the effectiveness of burns on disease prevalence. This is especially true with diseases that are primarily found to be transmitted to humans in a certain life stage of the tick, such as with nymphs and Lyme disease. Knowing the exact dates of the burns along with the time in between is useful when comparing the burn results to tick life cycles. For example, spring burns will mostly kill nymphs, although this can vary by species. Noting the geographic context is also important, as the environment plays a role in how these burn impact tick populations. Finally, increasing the time frame of studies that look at how prescribed fire impacts ticks will also be useful. Many studies that claim to study how ticks are affected by prescribed fires only involve a single burn, which is vastly different from true prescribed burning, which involves regular fires over many years.Land geography seems to have a role in the effectiveness of prescribed burns on tick population reduction regarding how fast the environment is able to regrow back to its original state before the burn, although to the best of our knowledge there have not been any studies that specifically look at this. Certain environmental factors might make certain geographic locations better candidates for prescribed fires when the main goal is to reduce tick populations, and this is a subject that is worth looking into in the future. It also appears that different tick species have different levels of heat and moisture resistance, causing them to be affected differently by the fires [12, 13]. Only very preliminary research has been done on this so far, although it is a topic that will substantially influence the choice of whether or not to use prescribed fires for tick reduction.


## 4.2. Conclusion

To conclude, in this study we develop a simple model for Lyme disease transmission and used it to investigate the impact of prescribed burn frequency and fire intensity on the spread of Lyme disease. To the best of our knowledge, this is the first model to incorporate the effect of fire into a mathematical model of ticks and Lyme disease. The key findings from this study are summarized as follows.The simulations of the Lyme disease model (A-5) with prescribed burns show that the following:(i)
The most influential parameters impacting the reproduction number,ℛ0, from the sensitivity analysis are πM,σT,K,μT,βT,βM.(ii)
Intensity appears to be a larger influence on tick reduction than duration is—it is better to burn fewer times at a high intensity than to burn more often at a lower intensity.(iii)
Burning at high intensity is preferable to burning at low intensity whenever possible, although the high intensity may be unrealistic due to environmental factors.(iv)
For low intensity, annual burns resulted in the most significant reduction in infectious nymphs, which are the primary carriers of Lyme disease.This study has shown the effect of prescribed fire on ticks and the spread of Lyme disease. In a future study, we will consider the impact of seasonality on the effectiveness of prescribed burns and the impact of the timing of the burns on disease spread. Geographic landscape and tick habitat are important factors affecting the tick population. In another future work, we will consider different types of geographic landscapes and determine which landscape is most effective in using prescribed burns for tick population control and reduction.



---

*Source: 5300887-2022-05-31.xml*