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The Spatial Distribution of Radiocesium Over a Four-Year Period in a Forest Ecosystem in North Fukushima After the Nuclear Power Station Accident

  • Masashi Murakami
  • Takahiro Miyata
  • Natsuko Kobayashi
  • Keitaro Tanoi
  • Nobuyoshi Ishii
  • Nobuhito OhteEmail author
Open Access
Chapter

Abstract

We have investigated the redistribution dynamics of radiocesium deposited after the nuclear power station accident in March 2011 in a forested catchment located in North Fukushima over a four-year period (2012–2015). At the catchment scale, 137 Cs accumulation decreased drastically by 50% of the estimated initial accumulation during the first 2 years. Cs-137 accumulation in the forest floor occurred in the litter layers and the surface part of mineral soils and have accounted for about 90% of the total catchment scale accumulation. The internal 137Cs cycle among the soil-plant system was also identified as a retention mechanism and was biologically dynamic. Monitoring the decreasing and retaining mechanisms of radioactivity at the ecosystem scale will be required for effective forest and water resource management.

Keywords

37Cs Inventory Environmental half-life Forest ecosystem Internal cycle Fukushima 

13.1 Introduction

The explosions at the Fukushima Daiichi Nuclear Power Station in March 2011 released a large amount of radioactive materials, especially iodine (131I and 133I) and cesium (134Cs and 137Cs), into the environment (Chino et al. 2011; Steinhauser et al. 2014). Half-lives of 131I and 133I are only 8.03 days and 20.8 h, respectively, but the half-lives of 134Cs (2.07 years) and 137Cs (30.1 years) are longer. Because of the long half-life of 137Cs, it is expected that 137Cs will pollute the surrounding natural environment for many years into the future.

About 70% of the Fukushima prefectural territory is covered by forests. The local communities have traditionally utilized the forests extensively not only for timber production but also for firewood and charcoal production before the 1960s. The collection of edible wild plants and mushrooms have also been a part of the traditional lifestyle of the residents for a very long time. It has been wildly recognized in Japan that local people have generally respected the environment and products of the forest ecosystem of this region (Fukushima Prefecture 2017). Therefore, it is critical for local people to precisely understand the quantity and distribution of radiocaesium in the forests and surrounding environment.

The first phase of the governmental surveys revealed that a major portion of the deposited radiocesium was trapped in the canopy of coniferous forests and in the litter layer on the forest floor of deciduous forests (Ministry of Education, Culture, Sports, Science and Technology; Ministry of Agriculture, Forestry and Fisheries 2012; Hashimoto et al. 2012). Within the forest ecosystem, radioactive materials deposited on the tree canopies subsequently moved to the forest floor by precipitation (Kinnersley et al. 1997; Kato et al. 2012) and litter fall (Bunzl et al. 1989; Schimmack et al. 1993; Hisadome et al. 2013). The movement of radiocesium from the canopy to the forest floor has gradually decreased (Hashimoto et al. 2013). Radiocesium has been shown to be easily adsorbed by clay minerals and soil organic matter (Kruyts and Delvaux 2002), which can be transported by eroded soil, particulates, and dissolved organic matter through hydrological channels, streams, and rivers (e.g., Fukuyama et al. 2005; Wakiyama et al. 2010).

Dissolved radiocesium, which is relatively free from soil adsorption, can also be taken up by microbes, algae, and plants in soils and aquatic ecosystems. By propagating through the food web in the forest ecosystem, it was expected that radiocesium would eventually be introduced into insects, worms, fish, birds and mammals. Many previous reports on the distribution and transfer of radionuclides have focused on their bioaccumulation and the transition between trophic levels (Kitchings et al. 1976; Rowan and Rasmussen 1994; Wang et al. 2000).

Our four-year monitoring study since early 2012 at a forested headwater catchment in the northern part of Fukushima have demonstrated that radiocesium movement has been most drastic during the early years after the accident (Ohte et al. 2013, 2016). Observed results have shown that radiocesium has continuously moved from the forest canopies to the forest floor with throughfall, stemflow and litter fall (Endo et al. 2015). It was found that fallen leaves and throughfall waters in the deciduous tree stands contain a certain amount of radiocesium since 2012. Since the attachment of deposited radiocesium did not occur directly onto leaves at the time of the accident in March 2011, because deciduous trees did not have new leaves, radiocesium inclusion in leaves in 2012 indicated that the translocation of radiocesium occurred in leaves from within the tree body (Endo et al. 2015). One of the possible sources of radiocesium transported to leaves was the deposited radiocesium in the litter layer on the forest floor. 137Cs in the organic layers (i.e, L, F and H horizons) of the deciduous stands ranged from 15 to 50 KBq m−2; these organic layers were the largest compartment where 137Cs accumulated in the forest ecosystem (Murakami et al. 2014). For radiocesium to be transferred via the food web in the same catchment ecosystem, the primary pathway was found to be the food chains originating from leaf and wood detritus, which was highly contaminated with radiocesium. Additionally, it was found that the decrease in 137Cs concentration was through trophic interactions, which was suggestive of biological dilution and not the accumulation of 137 Cs (Murakami et al. 2014).

During the past 4 years, while the total radiocesium accumulation has continuously decreased, its redistribution has proceeded by active transfers among compartments, such as transferring from canopy to litter layers on the forest floor. To develop a long-term future perspective in forest management, it is important to prepare a spatiotemporal prediction of radiocesium accumulation in the forest ecosystem. The aim of this paper is to summarize the time sequential changes in 137Cs accumulation in major compartments of the forest ecosystem and to discuss the mechanism behind the estimation of the catchment-scale environmental half-life of 137Cs accumulation.

13.2 Material and Method

13.2.1 Study Site

The study site was located at the headwater part of the Kami-Oguni River catchment in Date City, Fukushima prefecture, about 50 km northwest of the stricken nuclear power station (Fig. 13.1). Mean annual temperature in this region was 13 °C in 2012–2013 (Japan Meteorological Agency, 2012–2013), and the annual precipitation was 912 mm in 2012–2013 in this study site. Snow accumulation was observed every year, but annual maximum snow depth has been less than 60 cm during the period 1961–2017.
Fig. 13.1

Maps indicating the location of the study site at the Kami-Oguni River catchment. The study area was delineated with the geographic coordinates. These maps were attributed to Zenrin, Kingway Ltd., US Dept. of State Geographer, Mapabc.com, DATA SIO, NOAA, U.S. Navy, NGA, GEBCO, Cnes/Spot Image, and DigitalGlobe. (After Murakami et al. 2014)

The monitoring catchment (18.9 ha) has been set at the headwater part of the Kami-oguni river. The catchment is mainly covered by second-growth forests consisting mainly of deciduous tree species (e.g. Quercus serrata, Acer pictum, Zelkova serrata, etc.). Some Japanese red pines (Pinus densiflora) were found at the ridge part of the catchment. Deciduous trees in the second-growth forest have traditionally been utilized for charcoal and firewood production. Tree density of the second growth forests varied from 800 to 1300 ind. ha−1. Additionally, Japanese cedar (Cryptmeria japonica) plantations for timber production are situated at the lower part of the hill slopes. The age of the cedar plantation was about 50 years old; the stand density was 2100 ind. ha−1.

Two rectangular plots (20 × 20 m) in the second growth forest dominated by Q. serrata and one plot (10 × 40 m) in the Japanese cedar plantation was prepared for the vegetation survey. The height and diameter of all trees (at breast height) were measured to estimate the above-ground vegetation biomass.

According to a radioactivity survey report using an airborne survey device, the air dose rate and estimated 137Cs deposition were 1.9–3.8 μSv h−1 and 100–300 kBq m−2 in August 2011, respectively, which was 5 months after the accident. The dose rate has decreased to 0.5–1.0 μSv h−1 at (Ministry of Education, Culture, Sports, Science and Technology Japan 2017).

13.2.2 Sampling and 137Cs Concentration Measurements

To determine 137Cs accumulation in the major compartments of the target forest ecosystem, litter, soil and trees were sampled in May, July and September of each year from 2012 to 2015. Terrestrial and aquatic organisms including fungi, grasses, insects, soil worms, birds and small mammals were also sampled and had their 137Cs content measured at the same time. Because these terrestrial and aquatic organisms’ area-based biomasses were very small, we considered that their accumulation of 137Cs would be negligible for the catchment scale discussion. Thus, we defined the major compartments of the forest catchment for discussions on 137Cs redistribution within this ecosystem (Fig. 13.2).
Fig. 13.2

Sampled substances for determining the 137Cs distribution and redistribution mechanisms (in Italics)

All samples were dried for more than 48 h at 60 °C and powdered using a mortar and pestle. At least 200 mg of each sample was collected and 137Cs concentration was measured.

Litter and soil samples were collected from three points in the Q. serrata dominated stands and from two points in the C. japonica stands. Litter was separately sampled from the L, F and H horizons of the organic layer using a square frame (20 × 20 cm, 15 × 15 cm or 10 × 10 cm). Soil samples were taken from horizons at depths of 0–5 cm, 5–10 cm and 10–15 cm.

As tall trees in the stand were dominated by Q. serrata, two individuals of Q. serrata were cut down each year from 2012 to 2014 (one individual for 2015). One individual of C. japonica was also cut down from the C. japonica stands every year from 2012 to 2015. Leaves, branches, bark and wood (heartwood and sapwood) were sampled at every 2 m from the root side of sampled trees.

Gamma-ray spectrometry was conducted using germanium semiconductor detectors (Seiko EG&G) for 137Cs concentration measurements of all samples. An efficiency calibration of the detectors was made using volume radioactivity standard gamma sources (MX0333U8, Japan Radioisotope Association). Measuring accuracy was confirmed with the standard reference material JSAC-0471 (the Japan Society for Analytical Chemistry). The measured values were corrected for sampling day.

13.2.3 Estimation of 137Cs Accumulation and Its Environmental Half-Life

For litter layers and soil on the forest floor, the 137 Cs accumulation value of each compartment (Bq m−2) was estimated by multiplying the 137Cs concentration value by the dry weight of each sample and then dividing by the sampling area (the square frame for sampling).

Dry weight biomass of each tree part (i.e., leaves, branches, bark, heartwood and sapwood) was estimated from the vegetation survey using allometry equations developed for the forests in Fukushima and proposed by Kajimoto et al. (2014) and Hosoda et al. (2010). Then, the area based 137Cs accumulation as tree biomass (Bq m−2) was estimated by multiplying the average 137Cs concentration value with the dry weight of each component.

For estimation of total accumulation in the study catchment, we calculated the areal ratios of the Q. serrata dominated stands, the C. japonica stands and stream channels from the aerial photo image of the catchment. Then, the area-based accumulation of each compartment was estimated.

13.3 Results

13.3.1 Annual Changes of 137Cs Accumulation in Litter Layers, Soils and Trees

The total accumulation of 137Cs in forest floors decreased during the period 2012–2015 at both the C. japonica plantation and at the Q. serrata dominated stands (Fig. 13.3), while the initial distribution was significantly different between the two stands. This was because the deciduous trees had not leafed out when the accident occurred in March 2011. 137Cs accumulation in the litter layer of the cedar plantation site in 2012 was approximately 60% of that in the Q. serrata dominated stands (Fig. 13.3). This indicated that the canopies of the cedar trees captured 137Cs deposition effectively. While significant decreases were found in most layers from 2012 to 2014 at both stands, 137Cs accumulation in soils at a depth of 0–5 cm increased during 2014–2015.
Fig. 13.3

Area based 137Cs accumulation of litter layers and soil profile in (a) the Q. serrata dominated stands, and (b) the C. japonica dominated stands. (After Miyata 2017)

While the 137Cs accumulation was greater in the fresh leaves of the canopy than the other parts of the C. japonica tree, it was greater in the bark for the Q. serrata dominated stands (Fig. 13.4). The 137Cs accumulation in the cedar bark was significantly lower than that of Q. serrata. This indicated that the dense canopy of the cedar trapped the 137Cs deposition effectively and reduced the amount of deposition detected beneath the canopy.
Fig. 13.4

Area based 137Cs accumulation within the tree body in (a) the Q. serrata dominated stands, and (b) the C. japonica dominated stands. Close-up on the changes of 137Cs accumulation in the heartwood and sapwood of both stands were also shown. (After Miyata 2017)

It was notable that 137Cs accumulation in the heartwood and sapwood increased gradually during the period of 2012–2015, although the total accumulation of 137Cs in the bodies of trees decreased (Fig. 13.4).

13.3.2 Changes in 137Cs Accumulation in Each Compartment of the Catchment

Since 2012, 137Cs accumulation in most compartments decreased significantly in this catchment, except in surface soils and in heartwood and sapwood (Fig. 13.5). The largest accumulation has continuously existed in the litter layer and the near-surface mineral soils (0–15 cm). About 90% of total 137Cs accumulation of the catchment was held in the forest floor, and about 10% of that was retained in the above-ground living tree biomass. While the total accumulation has decreased one-sixth between 2012 and 2014, the proportion of the accumulation in the shallow mineral soils (0–5 cm) has increased during the same period. The accumulation itself has also increased in the 5–10 cm soils during 2014–2015 (Fig. 13.5).
Fig. 13.5

Area based 137Cs accumulation in organic layers, soil horizons (upper panel) and aboveground biomass (lower panel) in the study catchment including both the Q. serrata dominated stands and the C. japonica dominated stands. (After Miyata 2017)

13.4 Discussion

13.4.1 Redistribution of the 137Cs Accumulation

The increase in 137Cs accumulation in wood parts for both Q. serrata and C. japonica stands (Fig. 13.4) indicated that circulation occurred between trees and soils. 137Cs in the tree body was transported to leaves, and then it moved to the forest floor through litterfall. Decomposition of litterfalls releases 137Cs into the root zone within the organic and shallow mineral soil layers. This 137Cs could be absorbed by trees through their root system. This cycle has acted as a retention system of 137Cs in the forest.

At the interface between the litter layer and mineral soils, 137Cs has moved down from the H horizon to the surface part of the mineral soils in recent years (Fig. 13.3). Significant increases in 137Cs accumulation in soil depths of 0–5 cm during 2014–2015 could partly be explained by this mechanism. However, other accumulation mechanisms are required to be able to fully understand this drastic increase. One of the possible mechanisms was lateral input from the upslope parts onto the actual sampling points. Drifting of litter, for example, from upslope can supply extra 137Cs in addition to the vertical movement.

Several surveys have previously been conducted on the slope movement of deposited 137Cs and it was found that the movement with drifting litter and surface soil occurred occasionally by surface water flows and drifting snow accumulation (Kashihara 2014; Takada et al. 2017). As the soil layer for most of the catchment was established on the slopes, the 137Cs movement with drifting litter along hill slopes still needs to be researched quantitatively to estimate the catchment scale 137Cs accumulation precisely.

13.4.2 Catchment-Scale Environmental Half-Life of the 137Cs Accumulation

The environmental half-life of 137Cs accumulation in the entire catchment ecosystem was estimated from the fitted curve applied to yearly change based on the data in Fig. 13.4; the half-life was estimated to be about 2 years since July 2012 when the survey was initiated. This estimation was significantly shorter than the physical half-life of 137Cs, because of the washout effect on the deposited 137Cs in the first few years immediately after the accident. After 2014, the annual discharge of 137Cs through stream flow from this catchment was estimated to be 2–3 orders of magnitude lower than the initial deposited amount of 137Cs in this area (Iseda 2015). It was clear that the rate of decrease in 137Cs accumulation in watershed has further declined since then.

13.5 Perspective

The internal 137Cs cycle among the soil-plant system was clearly identified as a retention mechanism and was biologically dynamic. The increasing trend of 137Cs in sapwood and heartwood of Q. serrata has slowed. This might indicate that the 137Cs cycle between trees and soils was approaching a steady state condition.

Currently, the fixation with clay mineral in soils and the biological retention by the internal cycle among soil and plants are major factors retaining 137Cs in this forest catchment. Mechanisms that decrease 137Cs accumulation are the occasional discharge through streams via soil and litter particles during storm events, and physical decay. It is essential to continue to monitor the decreasing and retaining mechanisms carefully at the ecosystem level, because this information will be needed for careful consideration on radioactivity controls in forest and water resources management.

Notes

Acknowledgement

All data were collected during a research projects supported by a grant (24248027, 16H04934) for scientific research from the Ministry of Education, Culture, Sports, Science and Technology and with a grant for environmental researches from The Sumitomo Foundation. The authors would like to thank Mr. Chonosuke Watanabe for his kind help during the field work.

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Authors and Affiliations

  • Masashi Murakami
    • 1
  • Takahiro Miyata
    • 1
  • Natsuko Kobayashi
    • 2
  • Keitaro Tanoi
    • 2
  • Nobuyoshi Ishii
    • 3
  • Nobuhito Ohte
    • 4
    Email author
  1. 1.Graduate School of ScienceChiba UniversityChibaJapan
  2. 2.Graduate School of Agricultural and Life SciencesThe University of TokyoTokyoJapan
  3. 3.National Institute of Radiological SciencesChibaJapan
  4. 4.Department of Social Informatics, Graduate School of InformaticsKyoto UniversityKyotoJapan

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