The Correlation Between Butterfly and Flower Plant: Study for Ecology Sustainability

Green spaces with trees in urban areas are called urban forests. These areas can act as climate stabilizers, improve city aesthetics, serve as groundwater recharge zones, and offer shelter that supports environmental sustainability (Asri et al., 2023; Hadinoto et al., 2023). Trees in urban forests also serve as natural filters, absorbing pollutants and releasing clean air that benefits human health (Brito, 2023). Additionally, these habitats support various flora and fauna including butterflies (Ramirez-Restrepo and MacGregor-Fors, 2017). Such ecosystems provide the essential resources butterflies need to thrive, helping to conserve urban biodiversity (Sari et al., 2023).

Butterflies, a group of insects from the order Lepidoptera, are widespread and highly sensitive to environmental changes (Gunjan et al., 2024; Ismail et al., 2020). They serve as pollinators by feeding on floral nectar and are typically active during the day (Ghazanfar et al., 2016a, b). Since their presence and diversity both in terms of species and individuals depend on abiotic and biotic factors (Koneri et al., 2022), butterflies can function as bioindicators of environmental change in specific areas (Ricco et al., 2019).

The role of host and feed plants is crucial for butterflies, especially during their sub-imago and imago stages (Hailay et al., 2022; Irsa et al., 2022). Therefore, vegetation complexity in an area influences the species composition. It is also notable that brightly colored flowers with mild scents are more attractive to butterflies (Herlinda and Sari, 2023), so their budding flowers are more likely to be well-pollinated with their help. Pollinating insects are highly valued in agriculture and agribusiness because they improve both the quality and quantity of production.

Budianto and Sukendah (2023) stated that butterflies, along with other pollinating insect species, affect the pollination process of the castor plant (Ricinus communis L.). With a visit rate of over 50 %, butterflies also significantly enhance pollination for macadamia (Macadamia integrifolia Maiden and Betche) production (Santos et al., 2020). Lestari et al. (2023) stated that Phalanta phalantha (Drury, 1773), Eurema hecabe (Linnaeus, 1758), Genus: Tajuria sp. (Moore, 1881, and Jamides celeno (Cramer, 1775) are pollinators in Sandalwood plants (Santalum album Linn.) in the Purwodadi botanical garden, East Java, Indonesia. Maryuni (2018) reported that several butterflies are pollinators of watermelon flowers (Citrulus lanatus Thunb.). Sari et al. (2016) further detailed that there are 16 species of butterflies belonging to 14 genera and five families that play a role in pollination in watermelon plants.

Daawia et al. (2024) emphasized that butterflies play a role as pollinators in sustainable agriculture. They stated that Lycaenidae plays a role in helping pollinate horticultural plants such as Jamides soemias (Druce, 1891), Euchrysops cnejus (Fabricius 1798), Everes lacturnus (Godart, 1824), Catochrysops panormus (C. Felder, 1860), Zizula hylax (Fabricius, 1775) helps pollinate Momordica balsamina L. It was also stated that E. cnejus, E. lacturnus, and J. soemias help pollinate the Vigna unguiculata sesquipedalis (L.) plant. Eurema hecabe (Linnaeus, 1758) helps pollinate wild cucumber (Curcuma sp.) and cucumber (Crocus sativus L.). Eurema blanda (Boisduval, 1836), also helps pollinate C. sativus. The species E. hecabe, E. blanda, and Eupithecia puella (Mironov and Galsworthy, 2004) were also observed visiting and helping pollinate sweet orange (Citrus sinensis (L.) Osbeck) flowers, while Catopsilia pomona (Fabricius, 1775) and E. hecabe helped pollinate Cucurbita moschata (Duchesne).

Abiotic factors include microclimates related to habitat exposure that affect butterflies, such as temperature, humidity, and light intensity (Ambarli, 2024). A study on butterfly biodiversity in Srengseng urban forest was conducted in 2014 (Ruslan et al., 2020), while another study on environmental factors influencing butterfly biodiversity was completed in 2023 (Amalia, 2023). The authors repeated their survey in 2014 at the same place to check whether there was a population change after 10 yr. The reason for the re-observation was related to several studies that reported a decline in butterfly populations.

Warrena et al. (2021) reported that in the United Kingdom, 8 % of resident species have become extinct, and since 1976, overall numbers have declined by around 50 %. In the Netherlands, 20 % of species have become extinct; since 1990, overall numbers have declined by 50 %. In Flanders (Belgium), 20 butterflies have become extinct (29 %),

and between 1992 and 2007, overall numbers declined by around 30 %. Chowdhury et al. (2021) stated that the butterfly population in three urban parks in Dhaka City, Bangladesh, decreased sharply during 3 yr (January 2014 to December 2016). They feared that 40 % of butterfly species were threatened with extinction. Sulistyani et al. (2014) indicated that 19 types of Indonesian butterflies were threatened with extinction, while Ruslan et al. (2023) stated that there had been a 25 % decline in the abundance of butterflies in the Ragunan city forest (Indonesia).

Specifically, in the transition from forests to oil palm plantations, it was reported that butterfly species were lost (Ginoga et al., 2019; Hamer et al., 2015; Koh and Wilcove, 2008). Hamer et al. (2015) stated that species lost from 79 % to 83 %, while Ginoga et al. (2019) reported 15.79 % to 23.81 %. However, there was a butterfly species gain of 128.57 % to 136.84 % (Ginoga et al., 2019).

Several researchers (Chowdhury et al., 2021; Ghazanfar et al., 2016a, b; Mallick et al., 2023; Warrena et al., 2021) have stated that the decline in butterfly populations is due to the use of agricultural chemicals, the expansion of monoculture agriculture crops, and global warming. Chuan-ming et al. (2021) declared that the decline in butterfly populations is also due to the reduction in amino acids in flower nectar. Amino acid reduction (Setyobudi et al., 2023, 2024) occurs because absorption of nutrients and water is inhibited by microplastic (MPs) particles (De Silva et al., 2021; Setyobudi et al., 2025). The United Nations Environment Program (UNDEP) has designated global warming as the main danger to living things, while the second danger is MPs pollution due to the ubiquitous pollution (Loganathan and Kizhakedathil, 2023; Saati et al., 2025; Wahyudi et al., 2025).

This study explores the correlation between butterflies and plants in open and shaded habitats to understand biodiversity patterns, ecosystem health, also to provide insights into ecosystem transport-energy chain production. The continuing research can track how butterfly communities change over time, especially in response to ongoing urbanization and habitat transformation.

Many studies documenting the decline in butterflies with urbanization are not fully disentangled; more research is needed to clarify how these factors interact to shape butterfly communities in urban settings and to quantify the actual benefits butterflies provide to urban agriculture and green infrastructure. Furthermore, this research supports sustainable agriculture, particularly in its emphasis on the role of butterflies as pollinators (Bardales et al., 2017; Daawia et al. 2024; Rivest et al., 2023; Saldivar et al., 2022; Yek et al., 2024). It also supports the achievement of Sustainable Development Goals, particularly Goals 2, 3, 11, and 13 (United Nations, 2025).

Conducted from January 1 to March 10, 2024, butterflies within the area of Srengseng urban forest, West Jakarta, Indonesia (Figure 1, coordinate S 6°12’33.192” E 106°45’42.6024”) were observed.

Two habitats were pinpointed for the purpose: open habitat, which is exposed to direct sunlight with minimum shade from tall trees or buildings where plants can generally adapt to hot, dry conditions such as shrubbery or grass and flower plants are likely found (Figure 2), and shaded one which is blocked out from sunlight by either natural or artificial canopy where plants can generally adapt with humidity condition such as tall trees, vines, and undergrowth (Figure 3).

A purposive sampling plot was prepared for each habitat, which was monitored daily between 08.00 to 12.00 and 14.00 to 16.00 West Indonesian Time (WIB). The purpose was to align with the primary diurnal activity species under stable microclimatic conditions. The plot size was 20 m × 20 m and 10 m × 10 m

to present a commonly used unit in tree and shrub/herb-level vegetation sampling, allowing for the simultaneous assessment of butterfly-habitat structure that influences their distribution. Butterfly-feed plants were marked within the plot count. The unrecognized ones corresponded with the identification book (Engel and Phummai, 2002; Yudhono and Sukarya, 2013). Butterfly sampling was conducted using visual encounter surveys and photographic records. Observers stay in a fixed plot and record all butterflies seen within a set distance. Repeated data were used three times to ensure and enhance their utility for understanding diversity patterns at the microhabitat scale. Recognized species of butterflies and their quantities were collected, while unrecognized ones were captured or photographed before being matched with the identification book (Kirton, 2021; Peggie and Amir, 2006; Weei and Mun, 2008). This method is typically used for non-invasive and visible species, also non-destructive for rare or protected species.

Environmental parameters were measured every 2 h during research time 08.00 to 16.00, including humidity (%), temperature (°C), light intensity (lux), and wind speed (m s–1). The instrument was used digital Lux Meter Smart Sensor series AS803 includes a temperature and humidity sensor (range 0 to 200 000 lux, -10 to 50 °C, and 0 % to 100 %), and a digital wind anemometer series GM816 (range 0 m s–1

to 30 m s–1).

Assessment of butterfly composition: The composition of the taxa that comprise the butterfly community is assessed based on the number of taxa (class, order, family, and species) identified in the research area. The data are tabulated systematically to be directly compared between locations based on vegetation type.

Assessment of butterfly diversity index: The butterfly diversity index is based on species diversity based on Shannon-Wiener (Magurran, 1988), as shown in Equation 1.

H′ = − Σ pi ln pi, where pi = ni / N (1)

Notes: H′= Diversity index, ni= number of individuals of species i, N= Total number of individuals found.

The criteria used to determine the H’ value are as follows:

• Low = if the H’ value < 1.5

• Medium = if the H’ value is > 1.5 and < 3.5

• High = if the H’ value > 3.5

The species evenness index (E) is used to see the evenness of butterfly species. The Equation 2 based on Magurran (1988):

With: H’ max = maximum evenness index = In S

The range used in the evenness index is as follows:

0.0 < E ≤ 0.5: small population evenness

0.5 < E ≤ 0.75: medium population evenness

0.75 < E ≤ 1: high population evenness

The smaller the evenness index, the smaller the evenness of the butterfly population. It indicates that the distribution of the number of individuals of each species is not the same, so one individual tends to dominate. The greater the evenness value, it describes the distribution of the number of individuals of each type at each observation location as the same or not much different.

The importance of the dominance value index in butterflies are based on the abundance and distribution of a species in a habitat. The importance value index is based on the combination of relative abundance and frequency of presence of a species. Relative Abundance (RA) is based Brower et al. (1990). Abundance based on the proportion of a species using the Equation 3.

Relative frequency (FR) (Brower et al., 1990)

The distribution of a population is assessed based on the frequency of presence in various plots spread across a habitat. The frequency of presence value is determined based on Equation 4 (Krebs, 1985):

The important value index (IVI) (Fachrul, 2012).

IVI of butterflies is determined using Equation 5:

The correlation coefficient measures the strength and the linear relationship of two variables. To calculate the correlation, using Equation 6 (Sugiyono, 2020):

The value of the correlation coefficient (r) lies between -1 and +1

(-1 ≤ r ≤ +1)

If r = +1, there is a perfect positive correlation between variable X and variable Y.

If r = -1, there is a perfect negative correlation between variable X and variable Y.

If r = 0, there is no correlation between variables X and Y.

If 0 < r < +1, there is a positive correlation between variable X and variable Y.

If -1 < r < 0, there is a negative correlation between variable X and variable Y.

A total of 601 individuals from 43 butterfly species were recorded in the Srengseng urban forest. Based on the type of habitat in the Srengseng urban forest, a total of 401 individuals from 40 butterfly species were spotted in the open habitat, and 200 individuals from 27 butterfly species were spotted in the shaded habitat (Table 1).

Table 1: Butterfly composition in two habitats: Compared with the data from 2014.

Compared to observations made in 2014 (Ruslan et al., 2020), Table 1 shows an increase in the number of individuals and species, from 200 to 601 individuals and from 30 to 43 species, respectively. Several reasons for the rise are thought to be because of location, the abundance of food plants (Mallick et al., 2023), the availability of habitat for breeding (Kemmerling et al., 2023), and it could also be because the habitat conditions at the time of observation were stable (Wicaksono et al., 2023).

After 10 yr, the Srengseng urban forest has become denser, affecting abiotic factors, namely temperature and humidity. Likewise, more flowering trees can be fed to butterflies. Another thing is that the community, including urban forest managers, is increasingly knowledgeable and aware of maintenance so that ideal conditions are created for the development of butterflies.

Table 1 also shows that more butterflies live in open habitats than in shaded habitats. It is due to the abiotic aspects in Table 2. Abiotic factors, including temperature and humidity, affect the preference of butterfly species (Koneri et al., 2022). In addition, sunlight in open habitats allows more flowering plants to grow, becoming a significant food source for butterflies. As a result, the abiotic dynamics above shape an ideal area for flowering plants as a biotic reason for butterflies to live. Ruslan et al. (2023) also support this by stating that the survival rate of butterflies in a habitat is highly dependent on environmental factors.

Table 2: Abiotic factors in two habitats.

The diversity of plants in a habitat contributes to feed availability, making butterflies easier to find in open habitats than in shaded ones. Since biotic features of feed plant and host plant, as well as abiotic ones of temperature, humidity, and light intensity, are worthy for butterfly individual and species abundances in an area (Ambarli, 2024), it is deduced that the characteristics, including available resources, in both habitats are similar to each other.

The abiotic conditions between open and shaded habitats showed distinct differences, particularly in light intensity and temperature, while humidity and wind velocity were relatively similar (Table 2). The difference in wind velocity was minimal, suggesting that vegetation cover in shaded areas reduces wind flow only slightly. Both values indicate relatively low wind velocity, typical of near-ground microhabitats. Light intensity in the open habitat was more than double that of the shaded habitat. This reflects canopy cover reducing sunlight penetration, a critical factor influencing plant photosynthesis, butterfly activity, and microclimatic conditions. Humidity levels were virtually identical, suggesting that despite differences in canopy cover, the overall atmospheric moisture remained stable across both habitats. The open habitat was slightly warmer (+0.6 oC) than the shaded habitat. The difference is small but ecologically relevant, as higher temperatures combined with higher light may enhance butterfly thermoregulation and activity in open habitats.

The results of the calculation of the Shannon-Wiener diversity index (H’) and evenness index (E) in open and shaded vegetation habitats can be seen in Table 2.

Open vegetation habitats have a higher diversity index value (H’= 3.05) than shaded vegetation habitats (H’= 2.95). However, both diversity index values are moderate, between 1.5 and 3.5. The evenness index value approaching 1 in both habitats also indicates a high level of evenness of butterfly species in open canopy vegetation habitats (E= 0.83) and shaded (E= 0.90). The outcomes are listed in Table 3.

Table 3: Butterfly diversity index and evenness index values.

As for evenness values, an open habitat of 0.83 and a shaded habitat of 0.90 indicate that butterfly species are evenly spread the nearly 1.00 rates further represent high distribution in both habitats. The fact proves that an equally amiable quantity of resources is accessible in open and shaded habitats. This result corroborates the finding of Mas’ud et al. (2019) that the existence of highly preferred feed plants and host plants is paramount in maintaining butterflies in a habitat.

High species evenness is often positively correlated with ecological resilience, which is essential for sustaining biodiversity and ecosystem functionality. Evenness reflects how individuals are distributed across species in a community; when it is high, ecological roles are shared more evenly, preventing overdependence on a few dominant species. This balance supports functional redundancy, where multiple species contribute similarly to key processes like pollination, nutrient cycling, or pest control. As a result, ecosystems with high evenness can better withstand disturbances (e.g., climate fluctuations or habitat changes) and recover more quickly, as other species can compensate if one declines.

Moreover, high evenness may reduce the risk of invasive species establishment by limiting ecological niches and increasing community resistance. These findings align with the insurance hypothesis, which suggests biodiversity buffers ecosystems against environmental uncertainty (Yachi and Loreau, 1999). Therefore, promoting evenness alongside species richness in conservation strategies enhances not only biodiversity but also long-term ecological stability and resilience. This concept is particularly relevant in urban green spaces where fluctuating environmental conditions and human disturbance are common.

Butterfly species with high IVI values (dominant) indicate habitat conditions and plant availability that support the species’ survival. Three butterfly species with the highest IVI values in open habitats are: P. hebe (18.0 %), E. hecabe (17.3 %), and Z. otis (14.6 %). Three butterfly species with the highest IVI values in shaded vegetation habitats are L. nina (25.56 %), D. hyparete (21.11 %), and H. bolina (18.89 %). High IVI values can be caused by the presence of a butterfly species in all observation plots in the habitat. A high IVI value at a location indicates that the species has a vital role in the habitat, so it needs to be protected to maintain the sustainability of the ecosystem (Azizah et al., 2021; Sukma et al., 2021).

The three butterfly species with the highest IVI values in shaded canopy vegetation habitats were D. hyparete (22.4 %), P. polytes (21.5 %), and N. hylas (17.6 %) are the most seen species. Known to be able to live in various areas, including open environments, grassland, and woodland (Oo, 2020), D. hyparete should spawn well in shaded habitats. Additionally, its slow movement makes it easier to notice. P. polytes, Papilionidae family has a wider variety of host plants than other species (Peggie et al., 2022), allowing it to settle even in less warm areas. N. hylas, frequently spotted in oil palm plantations, can live in canopied surroundings (Ginoga et al., 2019), so the shaded habitat of the studied site is its natural territory. The adaptability of some species (e.g., D. hyparete, P. polytes, N. hylas) to various habitats, including open, shaded, and even disturbed environments, highlights their ecological flexibility and the importance of diverse habitat features for butterfly conservation.

Pearson correlation was used to analyze the relationship between the percentage of flowering plants (variable 1) and the number of individual butterflies (variable 2). Based on the calculation results shown in Figure 4, a correlation value of R= 0.76 was obtained. Referring to the correlation interpretation criteria according to Sugiyono (2020), this value indicates a strong relationship between the number of individual butterflies and the percentage of flowering plants in the two habitats observed.

Table 4: Vegetation in open and shaded habitat.

Table 5: Dominant larval host and nectar plants by habitat type.

Tables 4 and 5 shows that the flowering plant is focal in inviting butterflies to settle in a locale habitat (Haaland, 2023). The insect is generally attracted to flower scent and color, indicating nectar and pollen (Nursia et al., 2022). To ensure continuous butterfly pollination for biodiversity balance, providing conservatory spaces in diverse climatic conditions and vegetation is called for (Habel et al., 2022). Further, adapting the favorable characteristics of open habitat in urban landscape for both commercial and non-commercial produce should encourage butterflies to pollinate more and, in the end, optimize the transport energy chain in ecosystems that work naturally. Information on key pollinator issues i.e., feed and shelter should support a complete analysis of cover plant management, potential weed and herb cultivation, or other attempts to conserve pollinating insects like butterflies and bees.

Ecological challenges include climate conditions and vulnerability to pests and diseases. Based on environmental aspects and ecological sustainability, the success of a sustainable environment can be determined through the parameters of pest and natural enemy populations and beneficial insects. These are vital in sustaining ecosystem function and connectivity, such as pollinators that accelerate plant pollination, including butterflies, decomposers that recycle organic matter for soil fertility, and predators and parasitoids that control pests naturally. In addition, insects also function as bioindicators that provide an overview of the quality of the urban green landscape environment.

Larval host plants are often habitat-specific, with forests favoring woody species and open/urban habitats favoring herbaceous and sometimes non-native plants. Nectar sources are dominated by herbaceous perennials and flowering weeds (Asteraceae, Fabaceae), regardless of habitat, but diversity is highest in open and urbanized areas. Butterfly–plant interactions are dynamic, with some species adapting to non-native plants, especially in urban and disturbed habitats, highlighting the importance of plant diversity for butterfly conservation. The abundance and biodiversity of butterflies, with their connection to plants, play a key role in preserving mutualistic relationships while engaging communities in urban landscapes. For example, build an eco-tourism program centered on butterfly watching. It can involve local communities, promote environmental education, and support sustainable livelihoods that align with conservation goals.

Based on the study’s results, a total of 601 individuals from 43 butterfly species were found in the Srengseng urban forest. A total of 40 butterfly species, with a total of 401 individuals, were recorded in open habitats, while 27 species, with 200 individuals, were found in shaded habitats. The diversity index in both habitat types falls within the moderate category. Correlation analysis showed a powerful relationship between the number of butterfly individuals and the percentage of flowering plants (R= 0.76). It indicates that various biotic and abiotic factors influence the abundance of butterfly individuals in a given habitat. Furthermore, this study recorded more species and individuals compared to the findings in 2014, suggesting a possible improvement in habitat conditions or vegetation quality over time.

The authors would like to thank Universitas Nasional, Jakarta, Indonesia, for supporting this research and Srengseng Urban Forest Management, West Jakarta, for supporting data collection in the field. The authors also thank RP Editage for preparing and guiding this manuscript for publication.

Compared to observations made in 2014 (Ruslan et al., 2020), this study showed an increase in the number of individuals and species of butterflies. This research combines urban ecological data, microhabitat comparison, robust analytical methods, and real-world conservation implications contributing fresh insights into urban biodiversity conservation in tropical megacities. It provides updated data to underrepresented and rapidly changing urban areas in Southeast Asia. Most previous studies focus on rural, agricultural, or protected forest zones, making this urban focus a significant contribution to understanding urban biodiversity dynamics.

Hasni Ruslan: Conceptualizing and designing research, outlining the contents of the paper, conducting literature searches, collecting data, analyzing data, preparing the manuscript, and revising the manuscript.

Maizirwan Mel: Research supervisor and guarantor.

Nonon Saribanon: Assist in writing drafts and revising manuscript.

Imran Said Lumban Tobing and Dimas Mulya Pratama: Manuscript review.

All authors have read and approved the final manuscript.

The authors stated that they didn’t use generative AI and AI-assisted technology in preparing this manuscrip

The authors have declared no conflict of interest.