 Research
 Open Access
A model for solving the prescribed burn planning problem
 Ramya Rachmawati^{1, 2}Email author,
 Melih Ozlen^{1},
 Karin J. Reinke^{1} and
 John W. Hearne^{1}
Received: 16 June 2015
Accepted: 9 October 2015
Published: 21 October 2015
Abstract
The increasing frequency of destructive wildfires, with a consequent loss of life and property, has led to fire and land management agencies initiating extensive fuel management programs. This involves longterm planning of fuel reduction activities such as prescribed burning or mechanical clearing. In this paper, we propose a mixed integer programming (MIP) model that determines when and where fuel reduction activities should take place. The model takes into account multiple vegetation types in the landscape, their tolerance to frequency of fire events, and keeps track of the age of each vegetation class in each treatment unit. The objective is to minimise fuel load over the planning horizon. The complexity of scheduling fuel reduction activities has led to the introduction of sophisticated mathematical optimisation methods. While these approaches can provide optimum solutions, they can be computationally expensive, particularly for fuel management planning which extends across the landscape and spans long term planning horizons. This raises the question of how much better do exact modelling approaches compare to simpler heuristic approaches in their solutions. To answer this question, the proposed model is run using an exact MIP (using commercial MIP solver) and two heuristic approaches that decompose the problem into multiple singleperiod sub problems. The Knapsack Problem (KP), which is the first heuristic approach, solves the single period problems, using an exact MIP approach. The second heuristic approach solves the single period sub problem using a greedy heuristic approach. The three methods are compared in term of model tractability, computational time and the objective values. The model was tested using randomised data from 711 treatment units in the BarwonOtway district of Victoria, Australia. Solutions for the exact MIP could be obtained for up to a 15year planning only using a standard implementation of CPLEX. Both heuristic approaches can solve significantly larger problems, involving 100year or even longer planning horizons. Furthermore there are no substantial differences in the solutions produced by the three approaches. It is concluded that for practical purposes a heuristic method is to be preferred to the exact MIP approach.
Keywords
Background
Fire is a natural ecosystem process. However, uncontrolled wildfires can cause significant damage. Loss of human life, destruction of properties and natural resources are amongst the problems caused by wildfires (King et al. 2008). An increase in wildfire severity and extent has been observed in many countries such as the USA, Canada, Australia, and also in southern Europe (Boer et al. 2009). This is, to some extent, due to fire suppressionfocused twentieth century fire management practices, which according to Loehle (2004) and Reinhardt et al. (2008) results in uncharacteristically high fuel loads.
There are three key factors affecting fire behaviour: fuel, weather, and topography. Among these factors, it is acknowledged that only fuel can be actively controlled or managed (Schmidt et al. 2008). Finney (2007), Reinhardt et al. (2008) and Kim et al. (2009) also recommend reducing fuel load as the best possible way to slow fire growth. Fuel management is the process of altering the amount and structure of fuels through methods including prescribed burning and mechanical clearing (King et al. 2008). Fuel management is undertaken for wildfire hazard reduction as well as for ecological restoration (Reinhardt et al. 2008; Penman et al. 2011). Consequently, much effort is expended by these counties in the planning, prioritising and operational activities of prescribed burning.
Fuel management is a complex activity that involves both spatial and temporal decisions (Belval et al. 2014) and handling multiple fuel and ecological objectives. The development of decision support tools for fuel management programs is an ongoing and active research area (Martell 2011). Operations research (OR) has been successfully applied to a wide range of problems related to fire management, forestry management, and ecological management (Martell 2007) and offers great value in providing land management agencies with a framework for optimising fuel reduction planning over the landscape. A discussion of OR techniques used for solving fuel management problems can be found in the review paper by Minas et al. (2012). As an example, Wei et al. (2008) formulated an integer programming approach to reduce expected loss incurred on a landscape. Wei (2012) later proposed a mixed integer programming (MIP) method to locate fuel reduction treatments to set up potential control locations for future fires. Minas et al. (2014) later developed a model that deals with fuel treatment scheduling to break the connectivity of high risk treatment units applied in a landscape. However, a limitation of the models proposed, such as that by Minas et al. (2014), is that it only handles a single vegetation type, and fuel accumulation is treated as a linear function of time. In reality, the fire landscape is made up of multiple vegetation types, of mixed ages, with fuel accumulation taking on nonlinear functions depending on vegetation type. The model presented in this paper addresses these limitations by formulating a model within a landscape that consists of multiple vegetation types of mixed ages, with differing nonlinear fuel accumulation functions.
More recently, a review paper written by Chung (2015) highlighted the complexity of fuel treatments and examined previous fuel treatment optimisation studies to deal with it. Of note is that few studies incorporate the spatial and temporal dimensions of the problem. Perhaps more importantly is the conclusion that “most existing optimisation models suffer from problem complexity and a computationally intensive process ... making them almost impractical for field applications” (Chung 2015, p. 50). There is a clear need to understand the fitness for purpose of our models and to move beyond proof of concept applications. Do the tradeoffs warrant obtaining the perfect solution? Can we obtain a nearoptimal solution with heuristic approaches? To answer these questions, we illustrate both exact and approximate methods with a series of computational experiments with a case study of the BarwonOtway district of Victoria, Australia. We develop a MIP model for prescribed burn planning. The objective function of the model is to reduce fuel load accumulation in a landscape of multiage, multiple vegetation types, with differing nonlinear fuel accumulation functions.
The complex multiperiod model proposed in this paper can be solved exactly using an MIP solver or can be decomposed into singleperiod sub problems. The singleperiod sub problems are solved exactly using a solver and approximately using a greedy heuristic. With the exact MIP approach, an optimal solution can be achieved. However, the computational effort is costly. We introduce the two heuristics because the problem is NPhard. With the singleperiod heuristic approaches, less computational effort is needed, but the solution may not be optimal as the exact MIP approach. The three approaches for solving the model are compared in terms of model applicability, computational time and the objective values.
Model formulation
In this paper, candidate locations for fuel reduction burns are represented by ‘treatment units’. A treatment unit is defined as any area of land considered suitable for a planned burn treatment. Private land and water bodies, such as rivers and lakes, are considered nontreatable areas and are excluded from the model. Within the dataset, a treatment unit is represented as a spatial feature or polygon and contains additional attributes relating to the land ownership, vegetation types, vegetation ages and geometric properties, such as size, that exist within that treatment unit. The treatable area within the treatment unit is defined as the areas that have nonzero fuel loads.
The problem addressed by the model in this paper is where and when to conduct fuel reduction by minimising the total fuel load accumulation while still considering the ecological requirements of the vegetation present. The ecological requirements can be described as the minimum and maximum Tolerable Fire Intervals (TFI). The minimum TFI is defined as the minimum time required between two consecutive fire events at a location and is normally based on the time to reach maturity of the sensitive species in the vegetation class, while the maximum TFI refers to the maximum time needed between fire events at a location that considers the fire interval required for fireadapted species rejuvenation (Cheal 2010). A treatment unit should not be treated if the age of vegetation growing in that location is under minimum TFI. In contrast, treatment units with vegetation over the maximum TFI must be treated.
The prescribed burning planning problem in this paper is NPhard. The Knapsack Problem (KP), a wellknown NPhard problem (Garey and Johnson 1979), can be transformed to the 1year planning horizon Prescribed Burn Planning (PBP) problem in polynomial number of steps. The objective function of the KP is to maximise total profit, i.e. given a set of items, each with a weight and profit, determine the items to include so that the total weight is less than or equal to a given capacity limit. In order to transform KP into PBP, the capacity limit of the regular KP is changed to the burn limit. The items are transformed to the treatment units; the weight of the items is changed to the areas, and the profits become the fuel loads. The minimum and the maximum TFI of the problem are set to infinity.
We consider the landscape divided into treatment units. It is assumed that all the vegetation of each kind is of the same age within each treatment unit. With the decision to determine when and where to treat every year to minimise total fuel load of certain regions, the following MIP model is formulated.
 \(V_{i}\) :

is the set of vegetation types growing in treatment unit i
 T :

is the planning horizon
 C :

is the set of treatment units of which total fuel load is to be minimised
Indices:

i = treatment unit

j = vegetation type

k = vegetation age

t = period, t = 0, 1, 2, ...
Parameters:

\(w_{i}\) = relative importance (weight) of treatment unit i

\(m_{i,j}\) = the age of vegetation type j in treatment unit i at the beginning of the timeperiod

\(A_{i,j}\) = area (in hectares) of treatment unit i with vegetation type j

R = the total treatable area in a landscape

\(\rho \) = treatment level (in percentage), i.e. the maximum proportion of the total treatable area in a landscape selected for treatment

\(c_{i}\) = area of treatment unit i (where \(c_{i}=\underset{j}{\sum }A_{i,j}\))

\(L_{j,k}\) = fuel load (ton/hectare) of vegetation j, at age k

\(maxTFI_{j}\) = maximum TFI of vegetation type j

\(minTFI_{j}\) = minimum TFI of vegetation type j
Constraint (2) sets the initial conditions. Based on our observation of some raw data we felt it was necessary to include the possibility that the different vegetation types might differ in their ages. However, we assume that the all vegetation of a given type within a treatment unit will be of the same age. Constraint (3) indicates that when \(x_{i,t}=0\), which means fuel treatment is not conducted, the vegetation in that area will continue growing until the following period, and the age will be incremented by one.
Constraint (4) ensures that vegetation will be treated once it has reached maximum TFI. The vegetation with age 1 in the next period comes from the areas that are treated in the current period, as denoted in constraint (5). Constraint (6) ensures that in each timeperiod all vegetation of a specific type in each treatment unit will be of the same age. In reality, the same vegetation type within a treatment unit may have different ages resulting from wildfires that have burnt a treatment unit partially. However, we assume that there is a representative dominant age for each vegetation type in a treatment unit. Considering the possibility of multiple ages of the same vegetation type would be computationally prohibitive. Constraint (7) enforces that the vegetation under minimum TFI cannot be treated unless there is another vegetation type in the same treatment unit which is over the maximum TFI to avoid a deadlock. However, if required, this constraint can be changed to the other way, i.e. treatment units containing young treatment units cannot be treated. Here \(\mid V_{i}\mid \) represents the number of different vegetation types in treatment unit i.
Constraint (8) specifies that the total area selected for fuel treatment each year is not more than the annual area allotted (target) for fuel treatment (in hectares). Here, the target is obtained by multiplying the treatment level and the total treatable area in a landscape. Constraints (9) and (10) ensure that the decision variables \(y_{i,j,k,t}\) and \(x_{i,t}\) take binary values.
The model is capable of handling multiple vegetation types and ages. Each vegetation type has different minimum and maximum TFI, and at any period each vegetation type may have a different age even within a single treatment unit. The fuel curve representing each age of certain vegetation can also be a nonlinear function.
Solution approaches
An exact mixed integer programming (MIP) approach
The multiperiod model discussed in "Model formulation" can be solved exactly using an MIP solver. In this subsection, the model improvement is presented to enhance the solution time.
The solution time of a MIP problem can generally be improved by reducing the number of variables, or restricting the values that they can take. Age index k should be based on the set of possible ages that vegetation type j can take in treatment unit i at time t. The maximum possible periods between two consecutive treatments for any treatment unit can be derived by finding the minimum of the maximum TFI values of all vegetation types available within that unit. This sets an upper limit on the values k can take within that treatment unit.
We can also tighten the MIP formulation by introducing valid inequalities on the frequency of treatment event in each unit as follows
\(a_{i,j}\) = initial age of vegetation type j at treatment unit i
Singleperiod heuristic approach
In this subsection, two singleperiod heuristic approaches: an exact method for the singleperiod problem and an approximate method for the singleperiod problem are presented. These approaches, which are a single period 0/1 knapsack problem and a basic ‘greedy’ algorithm, are conducted as follows.
Consider I is the set of all treatment units in the landscape. The landscape is grouped into three disjoint sets: \(I_{old}\), \(I_{middle}\) and \(I_{young}\). The first set, \(I_{old}\), is the set of treatment units where at least one of the vegetation ages are over the maximum Tolerable Fire Interval (TFI). The second set, \(I_{middle}\), is the set of treatment units where the vegetation ages are between the minimum and the maximum TFI, and nothing is over maximum TFI. The third set, \(I_{young}\), is the set where all vegetation ages under maximum TFI and at least one vegetation under the minimum TFI. Here, \(I=I_{old}\cup I_{middle}\cup I_{young}\). Using these parameters,
\(A_{i}\) is area of treatment unit i
R is the total treatable area of the landscape
\(\rho \) is treatment level (in percentage),
then the value of \(r=\sum \nolimits _{i\in I_{old}}{A_{i}}\) can be determined. There are two cases that may arise when comparing the values of r and \(\rho R\).
Case 1: \(r\ge \rho R\)
If \(r\ge \rho R\), then \(x_{i}\) = 0, for \(i\in I_{middle}\cup I_{young}\). Either of these two approaches may be applied:
Using an exact method for the single period problem
Using an approximate method for the singleperiod problem
The treatment units are sorted based on the highest fuel load per area of treatment unit in the landscape, hence determining the rank or priority to burn. The treatment units then are selected by this rank until the burn limit requirement, \(\rho R\), is met.
"Using an exact method for the single period problem" provides an exact solution using Integer Programming and "Using an approximate method for the singleperiod problem" provides an approximate solution based on the exact solution of the continuous knapsack problem.
Case 2: \(0\le r<\rho R\)
If \(0\le r<\rho R\), then \(x_{i}\) = 1 for \(i\in I_{old}\). Either of these two approaches may be applied:
Using an exact method for the single period problem
The next step is to maximise (15) subject to (16) with i is defined only for \(I_{middle}\). Here, \(\rho _{new}=\rho \frac{r}{R}\).
Using an approximate method for the single period problem
The same process of ranking and selecting as with the Case 1 in "Using an approximate method for the singleperiod problem" is undertaken until the burn limit requirement, \(\rho Rr\), is met.
The approximate method can fail if we cannot use the capacity fully. The performance should get better if we have many small treatment units that we can burn to use the capacity (almost) fully.
Model demonstration
Consider a landscape divided into 40 treatment units. The area of each treatment unit, vegetation type and age are described in Table 1. The data regarding the minimum and the maximum TFI and the fuel type of each ecological vegetation class (EVC), can be seen in column two to five in Table 2. Figure 1 represents the fuel curve for each age of the certain vegetation type. Based on this data, some computational experiments were conducted to demonstrate three approaches: the exact MIP, the exact singleperiod and the approximate singleperiod problem. For the three approaches, we ran 5 and 10 % treatment levels, with and without TFI requirements. Figure 2 represents the fuel treatment schedule for the 5year planning horizon with TFI requirements. The total fuel load resulting from the experiments for the 5year planning horizon is represented in Fig. 3.
From these figures, it is clear that the 10 % treatment level results in less total fuel load than that of the 5 % treatment level. For this small landscape with the 5year planning horizon and with TFI, the three approaches show no substantial differences, which is most likely due to the relatively small feasible region. Without TFI requirements, the feasible region will be larger than if TFI is included. This larger feasible region makes the exact MIP approach superior to the other two approaches.
We also ran experiments for ten and 15year planning horizon with the three approaches, with and without TFI requirements. Table 3 represents the solution times and objective values for these experiments. The solution time rises as the length of the planning horizon expands. The approximate approach for the singleperiod problem has the lowest solution time of all, but the solution quality is also less than the other two approaches. In this small landscape, the exact approach for the singleperiod problem does not always outperform the approximate approach for the singleperiod problem, because of factors such as randomness and size of treatment units.
The results for the 5 and 10 % treatment levels with 10year planning horizon with TFI are described in Fig. 4. This figure shows that for each treatment level, the result of the exact MIP approach and the exact singleperiod problem shows no substantial difference.
40 treatment units data containing vegetation type, extent and age
Treatment unit ID  EVC code  Area (ha)  Age (years)  Treatment unit ID  EVC code  Area (ha)  Age (years)  Treatment unit ID  EVC code  Area (ha)  Age (years)  Treatment unit ID  EVC code  Area (ha)  Age (years) 

96  20  6.07  14  298  6  6.94  37  813  45  14.39  37  1093  48  13.15  37 
96  164  5.52  14  306  48  26.02  37  813  21  9.30  37  1093  161  12.81  37 
96  21  11.02  14  306  161  1.69  37  831  48  3.47  6  1093  163  1.15  37 
96  22  1.02  14  310  48  22.49  37  831  16  24.16  6  1107  22  23.59  2 
96  55  0.72  14  310  161  1.70  37  831  198  1.26  6  1107  47  1.48  2 
115  71  26.23  35  346  48  8.81  38  833  48  2.89  2  1121  20  26.43  6 
127  161  0.51  2  346  16  13.01  38  833  1  2.56  2  1125  20  14.15  5 
127  3  24.64  2  346  198  1.36  38  833  6  1.58  2  1125  22  13.20  5 
139  233  1.53  3  351  16  26.61  37  833  161  18.32  2  1130  20  27.54  14 
139  45  21.79  3  351  48  0.76  37  987  16  7.29  1  1134  16  13.79  3 
139  30  2.06  3  376  48  25.18  37  987  8  3.04  1  1134  20  1.60  3 
169  8  6.92  5  384  175  23.86  2  987  45  16.09  1  1134  22  7.72  3 
169  16  21.78  5  403  48  24.01  37  1033  45  25.74  81  1151  20  25.69  15 
180  45  25.79  8  477  16  24.76  6  1035  3  2.03  37  1152  20  18.74  4 
192  45  24.63  81  602  16  20.27  6  1035  161  17.48  37  1152  47  8.33  4 
236  16  5.96  5  602  48  2.59  6  1035  163  5.62  37  1171  851  3.39  3 
236  48  20.52  5  602  23  1.84  6  1049  16  7.97  16  1171  20  4.91  3 
277  16  26.95  52  634  16  27.27  36  1049  48  18.69  37  1171  22  19.55  3 
298  48  12.92  12  796  8  18.33  10  1081  48  14.97  25  1179  20  25.65  27 
298  161  5.28  37  796  48  10.25  10  1081  16  6.82  25  1181  16  19.08  8 
813  16  4.03  37  1081  178  2.22  55  1181  20  7.29  8 
Ecological vegetation class (EVC) and associated fuel types
EVC name  EVC code  Min TFI  Max TFI  Fuel type  Area (hectare)  Area (percentage)  Initial fuel load (ton) 

Creekline grassy woodland  68  20  150  7  6.14  0.008  65.08 
Hills herbrich woodland  71  15  150  7  641.42  0.872  6545.51 
Creekline herbrich woodland  164  15  150  7  281.36  0.383  2409.04 
Grassy woodland  175  5  45  7  141.44  0.192  1285.21 
Valley slopes dry forest  177  10  100  7  12.40  0.017  131.44 
Sedgy riparian woodland  198  20  85  7  532.54  0.724  4946.06 
Scoria cone woodland  894  4  15  7  20.74  0.028  219.84 
Wet forest  30  45  300  9  218.10  0.297  9396.53 
Shrubby wet forest  201  25  150  9  825.47  1.123  34,644.30 
Riparian forest  18  10  80  10  3.56  0.005  92.29 
Swampy riparian woodland  83  15  125  10  1.89  0.003  43.65 
Riparian scrub or swampy riparian woodland complex  17  10  80  11  2561.76  3.484  30,299.40 
Wet sands thicket  233  15  90  11  27.27  0.037  370.87 
Stream bank shrubland  851  15  90  11  38.32  0.052  521.15 
Cool temperate rainforest  31  45  999  1  0.60  0.001  5.88 
Wet heathland  8  12  45  13  1416.63  1.926  18,692.73 
Damp heath scrub  165  10  90  13  1142.88  1.554  15,908.60 
Damp heath scrub/heathy woodland complex  836  10  90  13  16.05  0.022  234.33 
Sand heathland  6  8  45  14  132.81  0.181  1684.73 
Clay heathland  7  10  45  14  30.58  0.042  405.60 
Coastal dune scrub or coastal dune grassland mosaic  1  10  90  1  253.84  0.345  3016.53 
Coastal headland scrub  161  8  90  1  1077.69  1.466  12,587.77 
Coastal headland scrub/Coastal tussock grassland mosaic  162  8  90  1  98.98  0.135  1177.86 
Coast gully thicket  181  10  90  1  1.67  0.002  15.52 
Coastal alkaline scrub  858  10  70  1  11.82  0.016  140.65 
Coastal saltmarsh/mangrove shrubland mosaic  302  8  90  2  4.52  0.006  14.46 
Coastal tussock grassland  163  5  40  3  260.27  0.354  3773.91 
Heathy woodland  48  5  45  4  15,985.16  21.738  313,589.23 
Shrubby woodland  282  10  45  4  220.56  0.300  3465.91 
Lowland forest  16  8  80  5  21,454.24  29.175  574,823.49 
Heathy dry forest  20  10  45  5  3958.52  5.383  95,741.43 
Shrubby dry forest  21  5  45  5  2299.87  3.128  64,937.21 
Grassy dry forest  22  5  45  6  2006.33  2.728  38,475.14 
Herb rich foothill forest  23  8  90  6  1670.13  2.271  34,302.81 
Shrubby foothill forest  45  8  90  6  12,945.85  17.605  258,807.84 
Herbrich foothill forest/shrubby foothill forest complex  178  8  90  6  2027.99  2.758  39,253.237 
Damp sands herb rich woodland  3  10  90  7  270.13  0.367  2776.23 
Valley grassy forest  47  10  100  7  397.99  0.541  4054.89 
Plains grassy woodland  55  4  15  7  482.38  0.656  4589.66 
Alluvial terraces herbrich woodland  67  4  15  7  56.07  0.076  594.34 
Total fuel load and solution time (seconds) or optimality gap (%) at 10,800 s, for 40 treatment units with 5, 10 and 15year planning horizon
Using the exact MIP approach  Using the exact method for the singleperiod problem  Using the approximate method for the singleperiod problem  

Treatment level  Treatment level  Treatment level  
5 %  10 %  5 %  10 %  5 %  10 %  
With TFI  
5Year planning horizon  
Solution time  0.28 s  0.61 s  6.36 s  6.96 s  0.01 s  <0.01 s 
Total fuel load (tonnes)  86,485.18  68,881.18  86,760.76  69,810.45  86,719.71  73,751.99 
10Year planning horizon  
Solution time  0.55 s  3.18 s  15.33 s  11.59 s  0.02 s  0.01 s 
Total fuel load (tonnes)  167,073.99  126,230.60  169,480.60  130,989.90  168,897.70  134,543.14 
15Year planning horizon  
Solution time  8.80 s  7586.33  20.54 s  16.06 s  0.03 s  0.01 s 
Total fuel load (tonnes)  245,671.97  185,310.04  250,616.10  193,569.77  250,348.40  195,460.34 
Without TFI  
5Year planning horizon  
Solution time  0.84 s  4.89 s  6.94 s  9.41 s  0.01 s  0.01 s 
Total fuel load (tonnes)  85,312.245  68,445.858  85,518.07  68,752.81  85,416.47  71,016.17 
10Year planning horizon  
Solution time  307.87 s  (0.58 %)  13.46 s  18.26 s  0.02 s  0.03 s 
Total fuel load (tonnes)  163,279.77  (123,346.30)  165,634.87  125,142.26  165,743.48  129,400.07 
15Year planning horizon  
Solution time  (4.59 %)  (8.82 %)  20.58 s  27.85 s  0.03 s  0.04 s 
Total fuel load (tonnes)  (242,727.28)  (180,937.79)  245,443.79  180,974.32  246,804.43  186,476.47 
An Australian case study
An Australian case study is presented to demonstrate the model. The study location is situated in the BarwonOtway district of Victoria, Australia, and covers approximately 1,150,000 hectares (Fig. 5a). Data used in this case study considers land ownership, vegetation type and age in each treatment unit, minimum and maximum TFI, and fuel load for the specific age of vegetation. In this case study, we categorise the treatment units according to land ownership (i.e. public or private). It is assumed that treatments can only occur on public land, so the candidate locations for prescribed burn planning are represented in these treatment units only. A total of 711 of treatment units exist over 73,535 hectares. Figure 5b shows the public land treatment units.
Using an exact mixed integer programming (MIP) approach
There are two phases when using this approach for the case study. Phase 1 (an exact method for the singleperiod problem) is a preliminary stage before the Phase 2 approach (an exact MIP approach) is executed. In Phase 1, the ‘old treatment units’ in the landscape are identified. The purpose of Phase 1 is to handle any infeasibility that might arise based on the initial data, by burning the old treatment units. This phase is necessary for ensuring feasibility of the Phase 2 approach. Infeasibility may arise due to conflicting constraints, especially constraints (4), (7) and (8). Constraints (4) and (7) in the Phase 2 approach require that all ‘old treatment units’ must be treated. However, treating all of these old treatment units (in this case, 35 % of the total treatable area in the landscape, as can be seen in Fig. 6a would violate Constraint (8) if the treatment level is set lower than 35 %. In practice, it would also be costly and impractical to treat such a large amount of land in a single year. Moreover, The 2009 Victorian Bushfires Royal Commission nominates a target of 5 % of the public land to be treated each year across the state in order to reduce the threat of fire for the coming fire season (Teague et al. 2010). Using a 5 % treatment level across the case study area means that imposing the maximum TFI leads to infeasibility of the Phase 2 approach. Therefore, to reduce the number of ‘old treatment units’ and achieve feasibility first, in Phase 1 the treatment level must be increased. For Phase 1 of the case study, a treatment level of 7 % of the total area of the landscape each year is imposed. Interestingly, (Penman et al. 2011) note that when more than 7 % of the total area has been burnt by prescribed fire, the total area burnt by unplanned fire will be close to zero.
Computational comparison between the three model configurations using a 5 % treatment level
Length of planning horizon (years)  Solution time (seconds) or optimality gap (%) at 10,800 sec  

Total  Subset  Random  
5  2.12  0.47  2.02 
10  43.19  6.31  37.06 
15  7819.6  46.23  3194.94 
20  (0.27 %)  80.79  (0.04 %) 
25  (5.45 %)  265.05  (1.02 %) 
In Phase 2, the exact MIP approach is applied to 10yearly planning horizons. The objective function is to minimise the total fuel load whilst meeting the constraints that have been described in "Model formulation". Figure 7 represents the result of Phase 2 and identifies the location of treatments for each year to minimise the total fuel load while satisfying the minimum and maximum TFI constraints. The length of the planning horizon is 10 years and the treatment level of each year is less than or equal to 5 %.
The model is solved using ILOG CPLEX 12.6.2 with the Python 2.7 programming language. Computational experiments are performed on Trifid, a V3 Alliance high performance computer cluster. We tested the original problem and noticed the solution time of the relaxed problem [using constraint (14)] is no better than the original most likely due to valid inequalities introduced by CPLEX. Based on that, we decided to use the original problem, not its relaxed version.
Computation time against different model configurations is tested and the results are represented in Table 4. The CPU time or the gap between the best solution identified and the current linear programming relaxation is presented. The solution may actually be optimal but CPLEX may need a long time to prove it. The three model configurations are: ‘total’ (total fuel load where all treatment units are considered equal), ‘subset’ (total fuel load where a subset of treatment units are prioritised) and ‘random’ (total fuel load where random weights are assigned to treatment units). In ‘total’, all \(w_{i}\)’s = 1. It means that the model minimises the total fuel load in all treatment units in the landscape, without prioritising certain regions. In ‘subset’, the value of \(w_{i}\) = 1 for some priority regions, and \(w_{i}\) = 0 for the other region. This priority may be due to proximity to towns. In ‘random’, 0 \(< w_{i} < \) 1 assigned a relative importance weight to treatment unit which may be based on the population at risk or any other measure of defining relative importance.
Using singleperiod heuristic approaches
Phase 2 can also be performed with the singleperiod heuristic approach for 5, 6 and 7 %. In Phase 2, the exact MIP approach provides a slightly better optimal solution (less total fuel load) than that of the singleperiod heuristic approach, as can be seen in Fig. 9. The differences between the exact MIP approach and the exact singleperiod heuristic approach for 5, 6 and 7 % treatment levels are 0.93, 0.94 and 1.02 %, respectively. However, using the exact MIP approach for the longer planning horizon, e.g. 100 years, is very difficult, while using the exact singleperiod heuristic approach a relatively good solution can be achieved in a reasonable computational time (\(<\)3 min for 100year planning). Because of their practicality, in the case study we then run the model with singleperiod heuristic approaches for 100 years.
In this case study, the computational experiments with or without incorporating TFI requirements are also conducted. The results for 5 and 10 % treatment level are represented in Figs. 10 and 11, respectively. By incorporating TFI requirements, when the treatment level is relatively high, e.g. 10 % annually, for some years the area burned may be less than 10 % in subsequent years. This is because the vegetation needs some time to regrow until it is eligible to be treated. The treatment units can only be burned if all of the vegetation types in the treatment unit are above the minimum TFI. Figures 10 and 11 also represent the results of excluding the TFI requirement, which the total fuel load in the landscape is relatively very stable. However, due to the importance of TFI as discussed in "Model formulation", in practice excluding these requirements is not recommended.
Conclusion
The purpose of this study was twofold. Firstly, to develop an optimisation method for scheduling prescribed burns, and to embed this in a realworld case study that takes into consideration the spatial and temporal complexity of the problem. Secondly, to consider the fitness for purpose of our models by comparing the performance of simpler, heuristicbased solutions to a more complex, optimisationbased solution.
The complex multiperiod model proposed takes into account multiple vegetation types of mixed ages in the landscape with differing nonlinear fuel accumulation functions. The model determines when and where to conduct fuel treatment to reduce the total fuel load in the landscape while still considering the ecological constraints relating to the Tolerable Fire Interval of each vegetation class. We compared the exact MIP and two heuristic approaches (Knapsack Problem and a greedy heuristic approach) in terms of the model tractability, computational time and the objective values.
The solution for a 15year planning horizon for the case study comprising 711 treatment units in the BarwonOtway district of Victoria was obtained in 2 h by using the exact MIP approach. With longer time periods it was not possible to achieve solutions of sufficient accuracy within a few days. While this approach can provide optimal solutions, it is computationally costly, especially for fuel management and ecological planning which may require longer planning horizons, and cover much larger geographic areas. Meanwhile, the heuristic methods can solve the problem for a longer times (e.g., 100 years), and the solution can be obtained in less than 3 min.
Based on our experiments, the singleperiod decomposition works well, and Knapsack MIP performs almost as well as the multiperiod MIP. For a 10year planning horizon with 5, 6 and 7 % treatment levels, the objective values resulting from these two approaches differs approximately by only 1 %. It is clear from the series of computational experiments that the solutions resulting from the heuristic approaches mimic that of the exact MIP to solve the prescribed burn planning model.
The results are an important reminder that future work may benefit from the use of heuristic approaches. Future research is planned to extend this study by incorporating other ecological requirements such as habitat connectivity within the landscape. However, particularly when using the exact MIP approach, this added complexity will increase computational effort to these problems as we increase the number of constraints and objectives built into our models. The case study shows that the heuristic approaches provide a nearoptimal solution and the computational time is significantly faster than that of the exact MIP approach. We conclude that for practical purposes a heuristic method is more than adequate.
Declarations
Authors’ contributions
RR planned the study, performed the computational experiment, and drafted the manuscript. MO helped to design the study, formulate and interpret the model, and helped to draft the manuscript. KR contributed to draft the manuscript. JH advised on model interpretation and helped to draft the manuscript. All authors read and approved the final manuscript.
Acknowledgements
The first author is supported by the Indonesian Directorate General of Higher Education (1587/E4.4/K/2012). The second author is supported by the Australian Research Council under the Discovery Projects funding scheme (project DP140104246). The authors thank the anonymous reviewers and the associate reviewer for their helpful comments that have improved this paper.
Competing interests
The authors declare that they have no competing interests.
Open AccessThis article is distributed under the terms of the Creative Commons Attribution 4.0 International License (http://creativecommons.org/licenses/by/4.0/), which permits unrestricted use, distribution, and reproduction in any medium, provided you give appropriate credit to the original author(s) and the source, provide a link to the Creative Commons license, and indicate if changes were made.
Authors’ Affiliations
References
 Belval EJ, Wei Y, Bevers M (2014) A mixed integer program to model spatial wildfire behavior and suppression placement decisions. Can J For Res 45(4):384–393View ArticleGoogle Scholar
 Boer M, Sadler R, Wittkuhn R, McCaw L, Grierson P (2009) Longterm impacts of prescribed burning on regional extent and incidence of wildfiresevidence from 50 years of active fire management in SW Australian forests. For Ecol Manag 259(1):132–142View ArticleGoogle Scholar
 Cheal D (2010) Growth stages and tolerable fire intervals for Victoria $$\hat{a}\breve{A}\acute{Z}$$ a ^ A ˘ Z ´ s native vegetation data sets. In: Fire and adaptive management report no. 84, Department of Sustainability and Environment, East Melbourne, Victoria, AustraliaGoogle Scholar
 Chung W (2015) Optimizing fuel treatments to reduce wildland fire risk. Curr For Rep 1(1):44–51Google Scholar
 Finney M (2007) A computational method for optimising fuel treatment locations. Int J Wildland Fire 16(6):702–711View ArticleGoogle Scholar
 Garey MR, Johnson DS (1979) Computers and intractability: a guide to the theory of npcompleteness. WH Freeman & Co, San FranciscoGoogle Scholar
 Kim YH, Bettinger P, Finney M (2009) Spatial optimization of the pattern of fuel management activities and subsequent effects on simulated wildfires. Eur J Oper Res 197(1):253–265View ArticleGoogle Scholar
 King K, Bradstock R, Cary G, Chapman J, MarsdenSmedley J (2008) The relative importance of finescale fuel mosaics on reducing fire risk in SouthWest Tasmania, Australia. Int J Wildland Fire 17(3):421–430View ArticleGoogle Scholar
 Loehle C (2004) Applying landscape principles to fire hazard reduction. For Ecol Manag 198(1–3):261–267View ArticleGoogle Scholar
 Martell D (2011) The development and implementation of forest and wildland fire management decision support systems: reflections on past practices and emerging needs and challenges. Math Comput For Nat Resour Sci (MCFNS) 3(1):18Google Scholar
 Martell D (2007) Forest fire management. In: Romero CC, Bjorndal T, Epstein RR, Miranda J, Weintraub A (eds) Handbook of operations research in natural resources. Springer, New York, pp 489–509Google Scholar
 Minas J, Hearne J, Handmer J (2012) A review of operations research methods applicable to wildfire management. Int J Wildland Fire 21(3):189–196View ArticleGoogle Scholar
 Minas J, Hearne J, Martell D (2014) A spatial optimisation model for multiperiod landscape level fuel management to mitigate wildfire impacts. Eur J Oper Res 232(2):412–422View ArticleGoogle Scholar
 Penman T, Christie F, Andersen A, Bradstock R, Cary G, Henderson M, Price O, Tran C, Wardle G, Williams R et al (2011) Prescribed burning: how can it work to conserve the things we value? Int J Wildland Fire 20(6):721–733View ArticleGoogle Scholar
 Reinhardt ED, Keane RE, Calkin DE, Cohen JD (2008) Objectives and considerations for wildland fuel treatment in forested ecosystems of the interior western United States. For Ecol Manag 256(12):1997–2006View ArticleGoogle Scholar
 Schmidt D, Taylor A, Skinner C (2008) The influence of fuels treatment and landscape arrangement on simulated fire behavior, Southern Cascade range, California. For Ecol Manag 255(8–9):3170–3184View ArticleGoogle Scholar
 Teague B, McLeod R, Pascoe S (2010) Final report, 2009 victorian bushfires royal commission. Parliament of Victoria, Melbourne Victoria, AustraliaGoogle Scholar
 Wei Y (2012) Optimize landscape fuel treatment locations to create control opportunities for future fires. Can J For Res 42(6):1002–1014View ArticleGoogle Scholar
 Wei Y, Rideout D, Kirsch A (2008) An optimization model for locating fuel treatments across a landscape to reduce expected fire losses. Can J For Res 38(4):868–877View ArticleGoogle Scholar