Residents’ Willingness to Pay for Forest Ecosystem Services Based on Forest Ownership Classification in South Korea

Abstract

South Korea is one of the countries with a significant proportion of its national territory covered by forests. However, it remains unclear what management strategies for providing forest ecosystem services are preferred by the residents. This study explores South Korean residents’ preferences for managing local forest ecosystem services, with a focus on how these preferences vary by forest ownership. Using the choice experiment method, this research identified residents’ willingness to pay for seven key local forest ecosystem services, along with a tax measure. The findings indicate a strong preference for biodiversity as the primary ecosystem service in both national/public and private forests, with residents willing to pay an average of KRW 28,370 (USD 21.80) per household per year and KRW 31,670 (USD 24.34) per household per year, respectively, for its enhancement. Preferences varied depending on forest ownership, with noticeable differences in perceptions of services like water supply, non-timber forest product supply, carbon storage, and recreation. Based on forest ownership, these variations in perceptions highlight the importance of managing ecosystem services in line with national/public forests and private forests, which significantly influences residents’ preferences. The study emphasizes the necessity of formulating ecosystem service management policies that account for the region’s unique natural resource characteristics, aiming to maximize ecological benefits for the local population.

1. Introduction

Forests cover 31% of the world’s land area and are crucial for maintaining global biodiversity. They serve as significant carbon sinks, thereby mitigating the impacts of climate change [1]. They also provide vital resources to local communities and offer non-utilitarian values, such as improving living conditions for urban populations [2]. Countries with extensive forest coverage value forests not only for their economic worth but also for their contributions to environmental conservation and cultural heritage, recognizing them as a key component of national welfare and sustainable development [3,4,5,6,7]. In South Korea, forests span 6,348,834 hectares, accounting for 63.2% of the total national territory, making it the fourth highest among OECD countries in terms of the percentage of forested land [8,9].

Korean forests perform various crucial roles, as defined in the ‘Forest Resources Management and Conservation Act’, including water resource cultivation, disaster prevention, environmental conservation, timber production, recreation, and living environment preservation [10,11]. These roles highlight the broad spectrum of ecosystem services forests provide, encompassing provisioning, regulating, cultural, and supporting services that offer direct and indirect benefits to humans, such as resources, climate regulation, and maintenance of biodiversity [12,13,14].

Individual preferences for these ecosystem services vary [15]. Tian et al. [16] identified several factors affecting private forest owners’ management of ecosystem services. These include forest tenure duration, individual preferences, and negative views on logging, all influencing the owners’ interest in ecosystem service management. Thus, preferences for ecosystem services vary according to diverse factors, including the socio-cultural characteristics and economic status of users [17,18]. For example, government authorities own and administer national/public forests, where carbon storage services are considered a crucial function and are primarily managed [19,20]. However, Thompson and Hansen [21] investigated the preferences of private forest owners for carbon storage services and discovered that only 37% viewed these services and carbon credits positively. This underscores the significance of aligning ecosystem services with user preferences [22,23,24].

The variety of ecosystem services provided by forests often varies according to their ownership classification [25]. In South Korea, forests are categorized into national forests, public forests, and private forests. As of 2020, national forests span 1.65 million hectares, constituting 26.2% of the total forest area. Public forests cover 0.48 million hectares (7.7%), while private forests account for the largest portion with 4.15 million hectares (66.1%). Despite the significant area covered by private forests, research focusing on the preferred ecosystem services relative to the ownership types of regional forests is lacking. Moreover, the strategies for managing local forests to cater to the specific preferences of residents remain undefined. This gap highlights the need for a thorough analysis of residents’ preferences for various types of forest ecosystem services [26,27].

1.1. The Tragedy of the Commons

Hardin’s ‘Tragedy of the Commons’ [28] concept highlights how individual exploitation of public goods can reduce their collective value. Unlike pasturelands, which are non-excludable and rivalrous, forests represent a unique case of being both non-excludable and non-rivalrous [29]. Non-excludable goods are those to which access cannot be restricted without incurring a cost [30], whereas non-rivalrous goods are those whose use by one person does not reduce availability for others [31]. However, managing these resources presents challenges, as competition for rivalrous goods leads to overuse and depletion, while even non-rivalrous goods face issues of overuse [32]. This competition and overuse can ultimately lead to the depletion and degradation of resources, exemplifying the ‘Tragedy of the Commons’ [28].

To mitigate the ‘Tragedy of the Commons,’ two main strategies are proposed: privatization and government intervention. Privatization suggests that individual ownership encourages efficient and conservational use of resources [32]. Alternatively, government intervention involves regulation by a central authority to protect natural resources [33]. While no consensus exists on the superior method, privatization is often preferred in subsequent research [34,35,36]. However, it is crucial to acknowledge that privatization may also lead to resource degradation by increasing individual disposability [37].

Ostrom challenged the privatization and government intervention strategies by emphasizing community participation as key to resolving the ‘Tragedy of the Commons’ [38]. She showed that communities with a deep understanding of the resource, management experience, cohesion, and regulatory capabilities can successfully manage resources [39,40]. Ostrom’s work suggests that effective management involves community-driven regulation and mutual oversight [41], underlining the importance of considering resource ownership types for tailored management strategies.

1.2. Ecosystem Services Valuation

The valuation of and preference for ecosystem services are shaped by regional characteristics, personal values, and experiences [12,13]. These preferences can be measured economically through willingness to pay, influencing policy decisions [42]. Ecosystem services fall into use values—direct, indirect, and option—and non-use values, including altruistic, bequest, and existence values [43,44].

Direct use values stem from consuming environmental goods, while indirect use values come from environmental processes like carbon absorption. Option values consider future resource use. Altruistic values reflect a desire for resources to be available to others, bequest values focus on preserving resources for future generations, and existence values appreciate environmental goods for their mere presence [45,46,47]. Forest ecosystem services are categorized accordingly, with provisioning and regulating services as use values, cultural services incorporating both use and non-use values, and supporting services as non-use values [48].

Ecosystem services are valued using methods like Stated and Revealed Preference, monetary valuation, benefit–cost analysis, cost-based approaches, and value transfer [49]. Revealed Preference, particularly through the Contingent Valuation Method (CVM) and choice experiments (CEs), is effective for valuing complex services like cultural and supporting ones [50,51]. CVM assesses non-market values but is limited to single attributes, whereas CE evaluates multiple attributes [52,53]. Jo et al. [54] used CE to study urban forest preferences in Seoul, highlighting biodiversity as a key value for residents, suggesting forest management should align with local preferences to enhance satisfaction and well-being. This underscores the importance of understanding resident preferences in forest management and planning [55,56].

Based on this background, the following research hypothesis is proposed:

Hypothesis: Residents’ preferences for ecosystem services will vary significantly between national/public forests and private forests.

Consequently, this study aims to explore preferences in managing ecosystem services, specifically examining how these preferences vary based on the ownership classification of local forests. By understanding the diverse preferences for ecosystem services based on forest ownership, this study aims to contribute to more effective and tailored forest management strategies.

2. Materials and Methods

2.1. Study Site

The study was conducted in Jeollabuk-do, Republic of Korea (Figure 1). This province, accounting for 8.04% of South Korea’s total area, is situated in the southwestern region of the country. The target population comprises residents living within this province. Jeollabuk-do is naturally separated from other administrative districts by the Sobaek Mountains to the east. The eastern part of the province is rich in forests, with regions such as Muju, Jinan, and Jangsu being predominantly mountainous terrain. In contrast, the western part is mostly composed of plains, especially the northwestern areas of Gunsan, Iksan, and Gimje, which have fewer forests compared to other cities. The province exhibits a terraced topography, higher in the east and gradually descending towards the west, and has a slightly longer east–west axis than its north–south axis [57].

As illustrated in Figure 2, forests in Jeollabuk-do are classified into national, public, and private forests. The region encompasses 103,117 hectares (23.4%) of national forests, 31,460 hectares (7.1%) of public forests, and a significant 306,169 hectares (69.5%) of private forests, highlighting the dominance of private ownership [58]. Additionally, considering the relatively smaller scale of forest administration in Jeollabuk-do than in other regions [59], there is a pressing need for efficient forest management. By examining the residents’ preferences for ecosystem services concerning the ownership of forests in Jeollabuk-do, this study aims to enhance management efficiency by aligning it with the residents’ preferred forest ecosystem services.

2.2. Choice Experiment

The choice experiment (CE) method, utilized in this study for preference analysis, falls under the Stated Preference methods used to evaluate the economic value of environmental goods. Stated Preference methods encompass both the Contingent Valuation Method (CVM) and choice experiments. Unlike CVM, which gauges value based on a hypothetical scenario for a single attribute of the target, the CE is distinct in its approach. It presents respondents with various alternatives that combine multiple attributes and levels. This setup enables a more comprehensive comparison of preferences across different attributes of the environmental goods in question [60,61].

2.2.1. Survey Design

This study focused on the residents of Jeollabuk-do as its subjects. As per the 2022 data from Statistics Korea [62], Jeollabuk-do’s population stands at 1,774,248, which represents 3.43% of South Korea’s total population.

For the choice experiment, seven attributes of ecosystem services were determined through an analysis of previous studies. The National Institute of Forest Science [63] conducted a literature review to identify representative attributes of forest ecosystem services in South Korea. They recognized key ecosystem services including provisioning services water and timber supply, soil conservation, carbon absorption, natural disaster prevention, recreational area provision, and biodiversity enhancement. Similarly, Jo et al. [54] investigated ecosystem service preferences in urban forests, identifying attributes such as water and timber supply, non-timber forest product supply, erosion control, carbon storage, water and air quality improvement, recreation, nature education, and biodiversity enhancement. Levels for each attribute were established based on findings from these previous studies.

The level of water supply provisioning was determined based on the ratio of deciduous to coniferous forests within the total forest area, following previous studies [64,65] that indicate deciduous forests provide a superior supply of water resources compared to coniferous forests. The level of timber supply was categorized based on the proportion of coniferous forests, as coniferous trees are considered more valuable as timber resources than deciduous trees, according to previous studies [66]. The level of non-timber forest product supply was classified based on the planting rate of forest products and fruit trees within the total forest area, guided by previous studies [54]. The ratios were categorized into three levels according to the FAO [67] criteria for forest type classification: less than 25%, between 25% and less than 75%, and more than 75%.

The level of erosion control was established based on previous studies [68], which argue that a higher understory coverage rate correlates with enhanced erosion control. Therefore, it was determined that forests with a high understory coverage rate would be considered to have a higher level of erosion control. The level of carbon storage varies according to forest stand type, species, and age [69,70]; therefore, the level of carbon storage was assumed to be consistent across characteristics such as forest type, species, age class, and stand density. Based on previous studies [71,72] that suggest a higher canopy density contributes to greater carbon storage, categorization was performed according to canopy density ratios [58].

The level of recreation was determined based on previous studies [73] that suggest a higher number of mountain sports activities available in forests indicates a higher level of recreation. Therefore, it was established that the more types and quantities of mountain sports activities that can be conducted in forests, the higher the level of recreation.

Given the importance of biodiversity and the general public’s difficulty in recognizing it [74,75,76,77], this study references Koo [61] to establish that higher species diversity and richness in forests indicate enhanced biodiversity.

To ascertain the willingness to pay, the attribute of tax was selected. Entrance fees or donations might be influenced by personal factors including site visitation frequency, marital status, and income level [78], making tax a more suitable choice. Forests are considered public goods with substantial non-use values [79] and provide a range of direct and indirect benefits to the general population. Consequently, tax was chosen as it more accurately reflects the public nature of forests and the universal benefits they provide. Referencing the amounts shown in previous studies [54,80], the willingness to pay for the enhancement of forest ecosystem services was set at KRW 10,000 per household per year, KRW 20,000 per household per year, and KRW 40,000 per household per year.

In identifying key ecosystem service attributes for this study, seven representative attributes provided by local forests were selected based on their recurrence in previous studies. Limiting the number of attributes is crucial as an excessive number can lead to confusion among respondents and complicate the analysis [81,82]. Phelps and Shantem [83] recommend, at most, exceeding eight attributes in such assessments. Common practice involves categorizing these attributes into three levels [84], with the importance of an attribute escalating as the number of levels increases [85]. Recognizing that attribute significance is amplified with more distinct levels, eight attributes were identified, each divided into three stages. This approach informed the categorization presented in

Table 1. The attributes and levels of local forest ecosystem services.

Attributes		Levels	References
Provisioning	Water supply	Low: less than 25% of deciduous trees Medium: 25% to less than 75% of deciduous trees High: more than 75% of deciduous trees	[64,65,67]
	Timber supply	Low: less than 25% of coniferous trees Medium: 25% to less than 75% of coniferous trees High: more than 75% of coniferous trees	[66,67]
	Non-timber forest products supply	Low: less than 25% of forest products and fruit trees planting Medium: 25% to less than 75% of forest products and fruit trees planting High: more than 75% of forest products and fruit trees planting	[54]
Regulating	Erosion control	Low: area covered by the forest 33% Medium: area covered by the forest 66% High: area covered by the forest 99%	[68]
	Carbon storage	Low: low canopy density (less than 40% canopy cover area by trees) Medium: medium canopy density (canopy cover area of 41~70%) High: high canopy density (more than 71% canopy cover area by trees)	[58,69,70]
Cultural	Recreation	Low: trekking Medium: trekking, camping, and climbing High: trekking, camping, climbing, MTB, paragliding, etc.	[73]
Supporting	Biodiversity	Low: poor Medium: average High: high	[61]
Tax	WTP for forest ecosystem service (Tax) (KRW/household/year)	Low: KRW 10,000 (USD 7.68) Medium: KRW 20,000 (USD 15.37) Rich: KRW 40,000 (USD 30.74)	[54]

KRW 10,000 = USD 7.69 (23 November 2023).

[80].

The regional forest ecosystem services selected for this study comprise eight attributes, each with three levels. This results in 6561 (3⁸) possible combinations. Given that studying all combinations is impractical and considering the likelihood of high correlations between attributes, an orthogonal design was employed to manage this complexity [86,87]. From this design, 27 alternatives were derived, and pairs were randomly formed to create 351 (₂₇C₂) different combinations. In the survey, respondents were presented with four combinations for each category of forest ecosystem services. In addition to alternatives 1 and 2, which displayed varied attributes and levels, a ‘Not selecting anything’ option was also included to allow respondents a choice to opt out. The purpose of this addition is to enhance the accuracy of responses by increasing the probability of respondents selecting the alternative they truly prefer [88].

In the survey, respondents were presented with descriptions and illustrations depicting the various attributes and levels of a hypothetical environment. This approach aligns with findings from Patterson et al. [89], who highlighted the effectiveness of hypothetical scenarios in surveys for capturing respondents’ attention and yielding significant results. Moreover, Bateman et al. [90] and Matthews et al. [91] have emphasized that visual aids in surveys contribute to more consistent responses from participants. Shr et al. [92] further observed that combining images and text to explain attribute levels in choice experiments can more effectively elucidate respondents’ preferences. Hence, for this study’s choice experiments, illustrations, compared to photographs, were chosen as the medium for presenting the attributes and levels of the hypothetical scenarios due to their ability to more straightforwardly convey the information (see Figure 3).

Various methods exist for estimating parameters in choice experiments, including the conditional logit model, mixed logit model, and latent class model. The conditional logit model is favored for its convenience in parameter estimation. However, it operates under the Independence of Irrelevant Alternatives (IIA) assumption. This implies that the presence or absence of other alternatives does not affect the choice between the options presented, which can be a significant limitation [93]. In contrast, the mixed logit and latent class models are more adept at capturing variations in respondents’ preferences but are less effective at highlighting preference diversity. For this study, the conditional logit model was employed. This decision was based on the fact that the independence of the alternatives was upheld, as evidenced by the results of the IIA test. This model was deemed appropriate given the specific requirements and context of the research.

2.2.2. Choice Experiment Theoretical Model

The theoretical background of choice experiments is based on McFadden’s [94] Random Utility Model, Hanemann’s [95] Discrete Choice Model, and Lancaster’s [96] Characteristic Theory of Demand [61,97].

According to the Random Utility Model, it is posited that a decision-maker selects the alternative that maximizes their personal utility from the set of available options. This model is expressed through an indirect utility function, which represents the utility of a respondent $n$ when they choose an alternative $i$. The specific formulation of this utility function is detailed in Equation (1).

$$U_{ni}=V_{ni}+e_{ni}$$

(1)

In the context of the Random Utility Model, $e_{ni}$ represents the utility component that is not accounted for by the characteristics of the goods. The importance of this variable lies in its role as the foundation for maximum likelihood estimation in statistical analysis.

Lancaster’s Characteristic Theory of Demand suggests that goods are essentially bundles of various attributes. According to this theory, respondents derive utility not directly from the goods themselves but from the combination of attributes these goods possess. The deterministic part of the utility, denoted as $V_{ni}$, is constructed as a linear combination of an attribute vector $X_i$, comprising $m$ attributes, as illustrated in Equation (2). This theory aptly aligns with the premise of choice experiments, where goods are assumed to be composed of multiple attributes, each contributing to the overall utility derived by the respondents.

$$V_{ni}=\sum _{k=1}^m{\beta }_k{X}_i$$

(2)

The Discrete Choice Model operates by presenting respondents with a set of options, from which they are asked to select one. This selection process is then utilized to explain or predict their choice behavior. The model calculates the probability that the nth respondent will prefer option $i$ over option j, as delineated in Equation (3). This probability is underpinned by the premise that the utility derived from choosing option $i$ is greater than that from choosing option $j$. This concept is rooted in the theory of utility maximization, which asserts that individuals make decisions in a manner that maximizes their personal utility.

$$P_{ni}=\mathrm{P}\mathrm{r}(V_{nj}+e_{nj}>V_n+e_{ni})$$

(3)

In the conditional logit model, as represented in Equation (4), $V$ signifies the contribution of attribute $i$ to the overall utility. This model assumes that the probabilistic component of choice follows the Gumbel distribution, also known as the Type-I extreme value distribution. This assumption is crucial for the estimation of parameter values within the model. The specific formulation of this probabilistic component is detailed in Equation (4) [93]. The Gumbel distribution aids in modeling the random variation in utility that cannot be explained by observable attributes alone.

$$P_{ni}=\frac{e^{V_{ni}}}{\sum _j{e}^{V_{nj}}}$$

(4)

3. Results

3.1. Characteristics of Respondents

This study aimed to gauge residents’ preferences for forest ecosystem services and their willingness to pay, thereby gaining insights into local preferences for regional forest ecosystem services. Prior to conducting the research, approval was secured from the Institutional Review Board (WKIRB-202307-SB-057). Data collection was carried out from 10 August to 14 August 2023. Residents of Jeollabuk-do aged 19 and above, who had resided in the area for over a year, were contacted via email for the survey. A total of 4177 emails were dispatched, resulting in 790 individuals accessing the survey link. After excluding responses from those outside the target demographic, those who exceeded the sample size limit, and those who did not complete the survey, an initial collection of 490 responses was obtained. Following a review process that identified and removed 90 insincere responses, a final dataset of 400 valid responses was compiled and analyzed (see

Table 2. Response status.

Status				Case Number (Person)	Proportion (%)
Survey link successfully sent	Received Survey link unchecked			3387	81.1
	Received Survey link checked	Out	Not targeted subject	83	2.0
			Exceeded targeted subject	154	3.7
			Incomplete response	63	1.4
		Response completed	Untrustworthy data	90	2.2
			Completed response	400	9.6
Total				4177	100.0

). The response rate for the survey was 50.63%, which meets the nonresponse rate criteria of 65% [98] and 70% [99].

The socio-economic characteristics of the respondents are detailed in

Table 3. Characteristics of respondents.

Category			Sample Size (%)	Proportion of Jeollabuk-do’s Total Population, as of 2020 (%)
Variables		Code
Age	20s	2	26.5	15.7
	30s	3	26.8	11.2
	40s	4	26.8	10.0
	50s and above	5	20.0	48.8
Sex	Male	1	50.0	49.8
	Female	2	50.0	51.1
Marriage	Single	0	52.0	12.0
	Married	1	48.0	88.0
Number of children	None	0	15.5	-
	1	1	13.3
	2	2	16.8
	3 above	3	2.5
Education	Less than middle school graduate	1	0.8	48.1
	High school graduate	2	12.3	29.2
	Attending or graduated university	3	73.0	21.0
	Graduate school student or graduate degree holder	4	14.0	1.7
Monthly household income	Less than KRW 1,000,000	0	6.3	21.7
	KRW 1,000,000 to less than KRW 2,000,000	1	5.5	18.3
	KRW 2,000,000 to less than KRW 3,000,000	2	21.0	20.2
	KRW 3,000,000 to less than KRW 4,000,000	3	16.8	14.7
	KRW 4,000,000 to less than KRW 5,000,000	4	14.3	9.5
	KRW 5,000,000 to less than KRW 6,000,000	5	14.3	6.4
	KRW 6,000,000 to less than KRW 7,000,000	6	8.0	3.5
	KRW 7,000,000 to less than KEW 8,000,000	7	6.3	1.8
	KRW 8,000,000 or more	8	7.8	3.9
Number of forest visits in the past year	None	1	24.8	-
	More than once	2	75.3
Purpose of visit	Forestry activities	1	0.3
	Relaxation/walking	2	46.5
	Nature experience(education)	3	1.0
	Physical activity	4	27.0
	Others	5	0.5

Source: adapted from Jo et al. [54].

. In reviewing these characteristics against the data from the Population and Housing Census by the Statistics Office and the Social Survey Report of Jeollabuk-do, we identified a notable discrepancy. The respondent demographics, with the exception of gender, did not entirely mirror the broader population of Jeollabuk-do. This disparity is a known limitation of online surveys [100]. Particularly, the lower internet access and usage rates among individuals aged 50 and above, largely due to lower digital literacy and accessibility among the elderly, contributed to a reduced representation of this age group in the survey responses. This aspect highlights a potential bias in the sample, which should be considered when interpreting the study’s findings.

3.2. Results of Estimation

In this survey, respondents were asked twice about their preferences for ecosystem services in both national/public and private forests. For each query, respondents were presented with a set of three alternatives, and this process was repeated four times. As a result, a total of 1600 data points were collected for national/public forests and an equal number for private forests, culminating in 3200 data points overall. The analysis of this data was carried out using R, specifically employing conditional logistic regression [101]. The results of this analysis highlighted distinct differences in preferences for ecosystem services between national/public forests and private forests. This indicates that the preferences of residents in Jeollabuk-do for forest ecosystem services are influenced by the type of forest, as detailed in

Table 4. The estimation results.

Ecosystem Service (Attributes)	Attributes and Levels	National/Public Forest (N)	Private Forest (P)	Hypothesis Testing (βN = βP) χ2 (1)
Alternative specific constant (ASC)		1.302 ***	1.568 ***
Water supply (Reference level: less than 25% of deciduous trees)	25% to less than 75% of deciduous trees	0.073	0.107	0.065
	More than 75% of deciduous trees	0.468 ***	0.183 *	4.921 **
Timber supply (Reference level: less than 25% of coniferous trees)	25% to less than 75% of coniferous trees	0.000	−0.084	0.437
	More than 75% of coniferous trees	0.077	0.041	0.080
Non-timber forest product supply (Reference level: less than 25% of forest products and fruit tree planting)	25% to less than 75% of forest products and fruit trees planting	−0.085	0.098	2.007
	More than 75% of forest products and fruit trees planting	−0.236 *	0.207 *	11.658 ***
Erosion control (Reference level: area covered by the forest 33%)	Area covered by the forest 66%	0.383 ***	0.415 ***	0.057
	Area covered by the forest 99%	0.697 ***	0.498 ***	2.356
Carbon storage (Reference level: low canopy density)	Medium canopy density	0.542 ***	0.123	10.181 ***
	High canopy density	0.627 ***	0.437 ***	2.149
Recreation (Reference level: trekking)	Trekking, camping, and climbing	0.226 *	0.337 ***	0.738
	Trekking, camping, climbing, MTB, paragliding, etc.	0.194 *	0.519 ***	6.214 **
Biodiversity (Reference level: poor)	Average	0.504 ***	0.380 ***	0.898
	Rich	0.745 ***	0.598 ***	1.271
WTP for forest ecosystem service (Tax) (KRW/household/year)		−0.022***	−0.015 ***

Significance level: * 10%, ** 5%, and *** 1%.

. The analysis incorporated a Log Likelihood test, which confirmed significant differences between preferences for national/public forests and private forests. Further hypothesis testing on specific attributes revealed notable differences in preferences for water supply, non-timber forest product supply, carbon storage, and recreation. In particular, ecosystem services like medium levels of water supply and carbon storage were more favored in national/public forests. Conversely, higher levels of non-timber forest product supply and recreational opportunities were preferred in private forests. These findings underscore the variation in preferences for local forest ecosystem services based on forest ownership type. They align with previous studies [102,103,104], reinforcing the argument for adopting diverse and tailored management strategies for different forest types to adequately address these varied preferences.

The analysis utilizing the conditional logit model revealed that, for national/public forests, the preferences of Jeollabuk-do residents were statistically significant for all attribute levels, with the exception of timber supply. These preferences significantly influenced the respondents’ choices, as detailed in

Table 5. Willingness to pay for ecosystem services in national/public forest.

Ecosystem Service (Attributes)	Attributes and Levels	Coefficient	z	p > z	MWTP (Unit: Korean Won (KRW))
					Mean	95% CI
Alternative specific constant (ASC)		1.302 ***	6.39	0.000
Water supply (Reference level: less than 25% of deciduous)	25% to less than 75% of deciduous trees	0.073	0.79	0.429	3339	−5127	12,379
	More than 75% of deciduous trees	0.468 ***	5.13	0.000	21,271	12,446	33,170
Timber supply (Reference level: less than 25% of coniferous trees)	25% to less than 75% of coniferous trees	0.000	0.01	0.996	0.021	−8405	8309
	More than 75% of coniferous trees	0.077	0.84	0.401	3511	−4745	12,317
Non-timber forest products supply (Reference level: less than 25% of forest products production and fruit tree planting)	25% to less than 75% of forest products and fruit trees planting	−0.085	−0.93	0.354	−3855	−12,420	4387
	More than 75% of forest products production and fruit trees planting	−0.236 *	−2.50	0.013	−10,719	−20,600	−2207
Erosion control (Reference level: area covered by the forest 33%)	Area covered by the forest 66%	0.383 ***	4.04	0.000	17,421	8733	29,122
	Area covered by the forest 99%	0.697 ***	7.50	0.000	31,667	21,928	45,975
Carbon storage (Reference level: low canopy density)	Medium canopy density	0.542 ***	5.67	0.000	24,618	15,279	37,450
	High canopy density	0.627 ***	6.65	0.000	28,517	19,001	42,076
Recreation (Reference level: trekking)	Trekking, camping, and climbing	0.226 *	2.41	0.016	10,250	1947	20,301
	Trekking, camping, climbing, MTB, paragliding, etc.	0.194 *	2.09	0.036	8836	0.486	18,453
Biodiversity enhancement (Reference level: poor)	Average	0.504 ***	5.42	0.000	22,896	13,703	35,699
	Rich	0.745 ***	7.99	0.000	33,844	23,710	48,961
WTP for forest ecosystem service (Tax) (KRW/household/year)		−0.022 ***	−7.08	0.000

Significance level: * 10%, and *** 1%; KRW 10,000 = USD 7.69 (23 November 2023).

. When it comes to the average willingness to pay (WTP) for changes in ecosystem service attributes, biodiversity was found to be the most valued. It was followed, in descending order, by carbon storage, erosion control, water supply, recreation, timber supply, and non-timber forest product supply. Notably, biodiversity attracted the highest WTP. Residents of Jeollabuk-do expressed a willingness to pay KRW 22,896 (USD 17.60) per household per year for an enhancement from a ‘low’ to ‘medium’ biodiversity level and an even higher KRW 33,844 (USD 26.01) per household per year for an improvement from ‘low’ to ‘high’ biodiversity level. Interestingly, the analysis revealed a unique trend in the willingness to pay for recreation services. While the WTP for an improvement from ‘low’ to ‘medium’ was KRW 10,250 (USD 7.88) per household per year, it surprisingly decreased to KRW 8836 (USD 6.79) per household per year for an enhancement from ‘low’ to ‘high’ level. This decrease in WTP, despite an increase in the level of service, highlights a complex valuation pattern for recreation services. In contrast, erosion control and carbon storage demonstrated increasing WTPs with higher levels of service. The WTP for erosion control rose from KRW 17,421 (USD 13.39) per household per year for a ‘low’ to ‘medium’ improvement to KRW 31,667 (USD 24.34) per household per year for a ‘low’ to ‘high’ improvement. Similarly, carbon storage’s WTP increased from KRW 24,618 (USD 18.92) per household per year to KRW 28,517 (USD 21.92) per household per year for the same respective improvements. Furthermore, the study noted negative values for non-timber forest product supply and tax attributes. This suggests that higher levels of these attributes were perceived negatively, adversely impacting the respondents’ choices.

In private forests, similar to national/public forests, changes in all attribute levels, excluding timber supply, were statistically significant and influenced respondents’ choices, as detailed in

Table 6. Willingness to pay for ecosystem services in private forests.

Ecosystem Service (Attributes)	Attributes and Levels	Coefficient	z	p > z	MWTP (Unit: Korean Won (KRW))
					Mean	95% CI
Alternative specific constant (ASC)		1.568 ***	7.45	0.000
Water supply (Reference level: less than 25% of deciduous trees)	25% to less than 75% of deciduous trees	0.107	1.18	0.239	6902	−4669	21,024
	More than 75% of deciduous trees	−0.183 *	2.03	0.042	11,881	0.581	27,492
Timber supply (Reference level: less than 25% of coniferous trees)	25% to less than 75% of coniferous trees	−0.084	−0.93	0.351	−5445	−18,722	6198
	More than 75% of coniferous trees	0.041	0.45	0.649	2648	−9260	15,796
Non-timber forest products supply (Reference level: less than 25% of forest product production and fruit tree planting)	25% to less than 75% of forest products and fruit trees planting	0.098	1.08	0.282	6360	−5628	20,058
	More than 75% of forest products production and fruit trees planting	0.207 *	2.33	0.020	13,408	1888	29,378
Erosion control (Reference level: area covered by the forest 33%)	Area covered by the forest 66%	0.415 ***	4.57	0.000	26,875	14,268	49,000
	Area covered by the forest 99%	0.498 ***	5.49	0.000	32,241	18,924	56,331
Carbon storage (Reference level: low canopy density)	Medium canopy density	0.123	1.36	0.173	7952	−3466	22,077
	High canopy density	0.437 ***	4.86	0.000	28,287	15,365	50,023
Recreation (Reference level: trekking)	Trekking, camping, and climbing	0.337 ***	3.73	0.000	21,846	10,066	40,975
	Trekking, camping, climbing, MTB, paragliding, etc.	0.519 ***	5.69	0.000	33,617	20,075	57,152
Biodiversity enhancement (Reference level: poor)	Average	0.380 ***	4.12	0.000	24,609	12,036	44,247
	Rich	0.598 ***	6.56	0.000	38,730	24,164	64,404
WTP for forest ecosystem service (Tax) (KRW/household/year)		−0.015 ***	−5.19	0.000

Significance level: * 10%, and *** 1%; KRW 10,000 = USD 7.69 (23 November 2023).

. The pattern of average willingness to pay (WTP) for changes in ecosystem service attributes differed from that observed in national/public forests. In private forests, the highest WTP was for biodiversity, followed by erosion control, recreation, non-timber forest product supply, water supply, carbon storage, and, lastly, timber supply. Notably, as in national/public forests, biodiversity was the attribute to the highest preference. Residents were willing to pay KRW 24,609 (USD 18.91) per household per year for an improvement from ‘low’ to ‘medium’ level and an even higher KRW 38,730 (USD 29.76) per household per year for an upgrade from ‘low’ to ‘high’. Contrary to the trend in national/public forests, where the WTP for recreation services decreased for higher levels of improvement, in private forests, the WTP increased to KRW 21,846 (USD 16.79) per household per year for ‘medium’ level and KRW 33,617 (USD 25.83) per household per year for ‘high’ level improvements. Similar to the findings in national/public forests, negative values were observed for timber supply and tax attributes in private forests, indicating that an increase in these levels had a negative impact on respondents’ choices.

4. Discussion

This study was initiated with the hypothesis that residents’ preferences for ecosystem services would vary according to forest ownership in Jeollabuk-do. Focusing on residents who have lived in Jeollabuk-do for more than a year and are aged 19 or older, it aimed to survey their willingness to pay (WTP) for improvements in forest ecosystem service levels. A choice experiment was conducted for this purpose, and data from 400 respondents were analyzed using the conditional logit model. Previous studies have either estimated preferences for ecosystem services for a single forest type [97,98] or focused on estimating ecosystem service preferences in major cities [54,105]. In this study, considering the ownership of forests, preferences for ecosystem services provided by regional forests were examined. While previous studies [54] examining the differences in preferences according to different forest types indicated no significant differences in preferences, Lapointe et al. [24] highlighted distinctions in ecosystem service preferences between urban and rural areas. The findings of this research underscore that residents perceive national/public forests and private forests differently. Specifically, residents in Jeollabuk-do showed a higher preference for national/public forests characterized by a substantial proportion of deciduous trees, lower ratios of forest products and fruit trees, high understory coverage and canopy density, and the availability of basic mountain sports activities such as hiking, camping, and climbing. A key factor contributing to this preference was the presence of rich biodiversity within these forests. Similarly, preferences for ecosystem services in private forests were higher in forests with a high proportion of deciduous trees, high ratios of forest products and fruit trees, high understory coverage and canopy density, the possibility of various mountain sports activities, and rich biodiversity.

When analyzing the preferences for ecosystem services in national/public and private forests regarding average willingness to pay (WTP), biodiversity was consistently the most preferred service, aligning with previous studies’ findings [54,106]. Jo et al. [54] reported that the willingness to pay (WTP) for improving urban forest biodiversity from ‘poor’ to ‘average’ levels was KRW 12,632 per household per year; for enhancing biodiversity from ‘poor’ to ‘rich’ levels, the WTP was KRW 21,645 per household per year. Muller et al. [107] found that citizens prefer improving species habitat services over recreational services, with an annual household WTP of KRW 54,291 for enhancing species habitat services. In this study, the average WTP for enhancing biodiversity in national/private forests from ‘low’ to ‘medium’ levels was KRW 28,370 per household per year; from ‘low’ to ‘high’ levels, the WTP was KRW 31,670 per household per year, indicating differences in WTP compared to previous studies. This suggests that biodiversity has become increasingly important over time [108], and differences in WTP may arise due to income level disparities between countries [109,110].

The erosion control service was universally favored, regardless of forest ownership. This preference is likely influenced by the increased occurrences of localized heavy rainfalls and subsequent landslides [111]. The survey was conducted right after the monsoon season, which could have heightened residents’ awareness and concern for landslide prevention and erosion control [112]. Although some ecosystem services like biodiversity and erosion control are universally preferred, other attributes demonstrated varying preferences depending on forest ownership.

4.1. National/Public Forest Ecosystem Services

The preference for the water supply service, when improved from ‘low’ to ‘high’, was notably higher in national/public forests than private forests. Although previous studies have suggested that water supply is more influenced by the proportion of forest area to total land area than by forest ownership [113], the actual perceptions of residents seem to diverge from this. National/public forests, primarily managed for nature conservation, likely influenced this higher preference for water supply services than the varied management goals of private forests [114,115]. Similarly, the preference for carbon storage services significantly increased from ‘low’ to ‘medium’ in national forests but not in private forests. This difference can also be attributed to the conservation focus in national/public forests, leading to a stronger preference for carbon storage services than in private forests. Carbon storage is significantly influenced by the methods of forest management and the intensity of harvesting [116]. Consequently, it is assessed that there is a relatively higher preference for carbon storage in national/public forests, where uniform management approaches can be applied, compared to private forests, where the objectives of forest management vary according to the owner.

Furthermore, it was noted that the willingness to pay (WTP) for recreation services was lower when improving from the ‘low’ to ‘high’ level compared to an enhancement from ‘low’ to ‘medium’. This trend is attributed to the residents’ perception that extensive mountain sports activities could lead to forest overdevelopment, thereby potentially harming the forest environment [73,117]. Many previous studies have reported that recreation has a negative impact on the natural environment. Steven et al. [118] reported that forest recreation activities such as hiking, mountain biking, and mountain horseback riding have negative effects on the environment. Evju et al. [119] reported that all trail-based activities cause damage to vegetation and soil.

In a similar vein, for the non-timber forest product supply service, WTP decreased as the level of the service increased. This decrease in WTP is believed to stem from the same concerns as those for the recreation service, where increased activity levels are perceived as potentially detrimental to forest health and sustainability. Moegenburg and Levey [120] reported that the management of non-timber forest products to meet market demand has a negative impact on forest ecosystems, while Albers and Robinson [121] found that the patterns of supplying non-timber forest products determine the level and pattern of forest cover and degradation.

Consequently, as indicated by previous studies, local communities consider the protection and conservation of national/public forests to be important [122], and recreation and the supply of non-timber forest products are less preferred compared to private forests; as the level of ecosystem service management increases, there is a potential for negative impacts on the forest environment.

4.2. Private Forest Ecosystem Services

In private forests, the carbon storage service, which was a high priority in national/public forests, ranked only sixth in terms of preference. Conversely, attributes like non-timber forest product supply and recreation services, which had lower WTP in national/public forests, exhibited higher values in private forests. This indicates that residents perceive private forests more as areas for the economic activities of the owners [123]. The trend for recreation services also differed from that in national/public forests; in private forests, the WTP was higher for an improvement from the ‘low’ to ‘high’ level than from ‘low’ to ‘medium’. This aligns with the findings of Sotomayor et al. [124], suggesting that people value diverse activities more in private forests than national/public forests. While timber supply has traditionally been a key function of forests, it was not significantly preferred by residents, and the WTP for this service was also low.

In the past, timber supply was a significant activity and one of the important functions of forests [125]. However, according to Levers et al. [126], the intensity of forest logging has significantly decreased compared to the past. Additionally, Heinonen et al. [127] reported that, as the preferences of private forest owners in Finland shifted towards conservation, the supply of timber decreased. It is believed that changes in environmental awareness have influenced the preference for timber supply through forest logging.

As shown in previous studies, changes in perception towards forests and shifts in societal values have influenced local communities’ preferences for ecosystem services. Carrus et al. [128] reported that people in modern society are increasingly recognizing the ecological and social values of trees and forests. Consequently, among various forest ecosystem services, biodiversity is the most preferred. However, it is recognized that private forests are places of economic activity for the owners; when visiting private forests, it is believed that people prefer to engage in different activities compared to national/public forests.

5. Conclusions

The results of this study offer substantial evidence for the development of forest ecosystem service management strategies that are aligned with residents’ preferences. It highlights that, since forest functions vary depending on the owners’ management objectives [129], customizing management strategies to reflect the type of forest ownership is crucial. Such tailored approaches can significantly improve the efficiency of managing local forest ecosystem services and budget allocations. Additionally, these strategies are likely to enhance the ecological utility for residents, ensuring that the management of forests is responsive to the needs and values of the local community.

As proposed in this study, forest ownership is an important factor to consider in forest management. For instance, for the successful implementation of forest projects like REDD+, local governance is crucial [130,131], and successful local governance requires considering forest ownership. The REDD+ Safeguard Information System (SIS) also includes elements such as forest governance and respect for the rights of residents, making it important to reflect their preferences [132]. Therefore, it is necessary to manage forest ecosystem services based on whether forest ownership lies with the state or with other individuals, including residents, and to consider the preferences of residents in the project areas in light of forest ownership. By doing so, we can establish local governance that involves the local community in the management of forest ecosystem services, leading to the successful execution of forest projects.

A notable limitation of this study is that the sample does not fully represent the population. The survey was conducted online, resulting in a lower representation of respondents aged 50 and above, who constitute a significant portion of the rapidly aging population in Jeollabuk-do. Additionally, conducting the survey in regions outside of metropolitan areas like Seoul limited the availability of a diverse sample, which can be considered another limitation. When conducting surveys, especially considering the accelerating depopulation in rural areas, efforts to maximize sample collection through face-to-face surveys, using local communities, and conducting Gang surveys instead of relying solely on online methods are deemed important.