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Note that a Preprint of this article also exists, first published April 17, 2016.

Introduction

Accidentally-introduced insect pests have caused major economic losses and environmental damages within the US (Pimentel, Zuniga & Morrison, 2005). Examples include the elm bark beetle (Scolytus multistriatus Marsham), which has spread Dutch elm disease in North America and killed an estimated 75% of all the elms (Ulmus spp.; Kendrick, 2000), and the balsam woolly adelgid (Adelges piceae (Ratz.)), which has severely damaged the spruce-fir forests of southern Appalachia, killing up to 95% of the Fraser fir trees (Abies fraseri (Pursh) Poir) and substantially changing the avian community (Rabenold et al., 1998; Gandhi & Herms, 2010).

Two accidentally-introduced ambrosia beetles are threatening to cause similar ecosystem-wide damages to the riparian habitats of southern California. These beetles are the Polyphagous Shot Hole Borer (PSHB; Euwallacea sp. near fornicatus; Coleoptera: Curculionidae: Scolytinae) and the Kuroshio Shot Hole Borer (KSHB, Euwallacea sp.; Eskalen, 2016). The two species are morphologically identical and are distinguished by their DNA sequences and by their associated fungi (Eskalen, 2016). They are part of a species complex that also includes the Tea Shot Hole Borer (Euwallacea fornicatus (Eichhoff)). The PSHB was first documented in Los Angeles County in 2003, and the KSHB was first observed in San Diego County in 2012 (Eskalen et al., 2013; Eskalen, 2016; Umeda, Eskalen & Paine, 2016). Both are believed to be native to Southeast Asia and both attack many tree species in southern California, including native species, landscape trees, and the economically important avocado (Persea americana Mill.; Freeman et al., 2013; Eskalen et al., 2013). The ever-increasing list of reproductive host plants used by these species is currently at 41 species for the PSHB and 15 species for the KSHB (Eskalen, 2016).

Both ambrosia beetles were initially observed to cause problems in urban and agricultural settings, but their recent appearance in natural settings has raised grave, new concerns. Both damage or kill trees through their boring activities and their spread of fungal pathogens. Females bore into tree trunks, create networks of tunnels in the xylem, inoculate the tunnels with a fungus (e.g., Fusarium sp.), and live in the tunnels eating the fungus and reproducing (Biedermann, Klepzig & Taborsky, 2009). Within a few weeks females emerge, fly to new trees, and perpetuate the infestation (Rudinsky, 1962). Most trees appear to die from the fungal infection in their tissues (Freeman et al., 2013). Beyond this life cycle, little is known about the effects of any ambrosia beetle in natural habitats because the emphasis of research investigations has been on their presence as pests of commercial agriculture and lumber rather than in natural areas (Wood, 1982; Hulcr & Dunn, 2011).

In late summer 2015, the KSHB was found in the riparian forests of the Tijuana River Valley, making these forests the first natural habitats in California to be substantially attacked by an invasive ambrosia beetle. These forests are dominated by two willow species, Salix lasiolepis Benth. (arroyo willow) and Salix gooddingii C.R. Ball (Goodding’s black willow), which account for more than 80% of the individuals and create the vertical structure of the forest (Boland, 2014a). Both willows were attacked by the KSHB and, within only a few months, tens of thousands of trees were visibly infested. The forests were so obviously negatively impacted by the beetle that the infestation was covered by the local news media (e.g. Graham, 2016; Smith, 2016).

Here I describe the distribution of the KSHB in the riparian habitats of the Tijuana River Valley during the six-month period after first observation, assess the damage caused by the beetle, and discuss the prospects of the habitats recovering from this unusual damage. The overarching goal of this paper is to alert resource managers to this emerging beetle problem in natural habitats.

Study Site

The Tijuana River Valley (32°33.080′N, 117°4.971′W) in San Diego County, California, is a coastal floodplain of approximately 1,500 ha at the end of a 448,000 ha watershed (Fig. 1). The river is a managed intermittent stream that typically flows strongly in winter and spring and is mostly dry in summer (Boland, 2014a). In 2015, however, the main river channels contained water all summer because of unusual rain storms on May 7, 15, July 18 and September 15. The main river splits into two in the center of the floodplain at Hollister Bridge, and the northern arm carries more of the flows than the southern arm because of extensive sedimentation west of Hollister Street within the southern arm.

Map of the Tijuana River Valley.

Figure 1: Map of the Tijuana River Valley.

The location of the riparian forest and riparian scrub habitats within the Tijuana River Valley.

Riparian forests in the river bed are numerically and structurally dominated by S. lasiolepis and S. gooddingii, and the surrounding riparian scrub is numerically and structurally dominated by the perennial shrub, Baccharis salicifolia (Ruiz & Pav.) Pers. (mule fat; Boland, 2014a). Zonation of these three dominant species across the elevation gradient and the factors that produce their zonation were described in Boland (2014a).

The riparian forest and scrub habitats are preserved within three adjoining parks: the Tijuana River Valley Regional Park, the Border Field State Park, and the Tijuana Slough National Wildlife Refuge. The riparian habitats are relatively undisturbed and support numerous reptile, mammal and bird species, most notably the endangered Vireo bellii pusillus Coues (least Bell’s vireo) for which most of the riparian habitats are designated critical habitats (US Fish and Wildlife Service, 1994).

The beetles causing the damage in the riparian habitats of the Tijuana River Valley during 2015–16 were collected and identified as the KSHB by Dr. Akif Eskalen at University of California Riverside (UCR; Eskalen, 2016). These specimens have been stored in the UCR collection.

Materials & Methods

Infestation and damage rates in the valley

To estimate the extent and magnitude of infestation and damage in the valley, I surveyed the entire valley in a stratified random manner. I divided the valley’s riparian forest and scrub habitats into 29 survey units so that the vegetation within each was relatively homogenous in terms of plant species composition, age and density. Within each unit, an accessible survey point was chosen at random from among several accessible points. The location of each survey point was recorded using a handheld GPS unit (Garmin eTrex Venture HC) and the units were mapped (ArcGIS 10.2.2. and projected in Universal Transverse Mercator). I did four surveys in each unit focused on the dominant plant species, S. lasiolepis and S. gooddingii in the forest units, and B. salicifolia in the scrub units.

First, I examined S. lasiolepis, S. gooddingii and B. salicifolia for evidence of KSHB infestation, using binoculars when necessary. A plant was counted as infested (or attacked) if it had beetle holes, extrusion of sawdust plugs or frass, or gumming out of sap (Figs. 2A2D). Plants with only weeping were noted but included with the non-infested plants in the final count (Hulcr, 2012). All plants examined were within 50 m of the survey point. Surveys were conducted between November 2, 2015 and January 22, 2016. The rate of infestation (the percent infested) was calculated for each forest unit based on S. lasiolepis and S. gooddingii and for each scrub unit based on B. salicifolia.

Photos of the KSHB in the Tijuana River Valley.

Figure 2: Photos of the KSHB in the Tijuana River Valley.

(A) Two beetles at the entrance to a tunnel. (B) Holes in the bark of a sycamore. (C) Extrusion of sawdust plugs indicating active burrowing within an arroyo willow. (D) Gumming out of beetle holes in mule fat. (E) Beetle tunnels and associated fungus (black staining) in a cross section through a black willow trunk. (F) Beetle-infested trunks of arroyo willows snapped by the wind.

Second, I examined S. lasiolepis, S. gooddingii and B. salicifolia for evidence of major plant damage. A plant was counted as damaged if it had a recently-broken trunk or major limb (Fig. 2F). All plants examined were within 50 m of the survey point. These surveys were conducted after the first winter storms, between December 14, 2015 and January 22, 2016. The rate of damage (the percent damaged) was calculated for each forest unit based on S. lasiolepis and S. gooddingii and for each scrub unit based on B. salicifolia.

Third, within the forest units I measured the girth of the S. lasiolepis and S. gooddingii trees at breast height. All plants measured were within 50 m of the survey point. An average of 33 (±7) trees was measured in each unit, and the median value within each unit was determined.

Fourth, I recorded the species composition and density of all plant species. All perennial trees and shrubs taller than 0.5 m were identified and counted within a belt transect (20 m × 2 m = 40 m2) that started at the survey point. Transects were done between November 2, 2015 and January 22, 2016. To estimate the total number of S. lasiolepis and S. gooddingii individuals in each forest unit and the total number of B. salicifolia individuals in each scrub unit, the density of these species in the transect was multiplied by the area of the unit. The numbers of individuals infested and damaged in each unit were then extrapolated by multiplying the total number of individuals by the infestation and damage rates in each unit.

Finally, I assigned a measure of wetness to each unit based on the distance of the survey point from surface water during summer 2015. The measure was used to test whether infestation rate in a site was correlated with the relative wetness of the site.

Infestation rates in the common plant species

I examined all common tree and shrub species for signs of infestation when they were encountered while doing the surveys above. As above, a plant was counted as infested if it had beetle holes, extrusion of sawdust plugs or frass, or gumming out of sap, whereas plants with only weeping were noted but included with the non-infested plants in the final count. In total, 23 species were examined, and the rate of infestation (the percent infested) was calculated for each species.

Results

Infestation and damage rates in the valley

Evidence of KSHB infestation was widespread throughout the valley, being observed in all but four of the 29 survey units (Table 1). Rates of infestation were high (61–100%) in 16 of the 22 forest units (Units 1–14, 19, 22). Most of the S. lasiolepis and S. gooddingii in these units had obvious sawdust and frass coming out of abundant holes indicating active boring of the beetles within. Rates of infestation were low (0–10%) in six of the forest units (Units 15–18, 20–21) and in all of the scrub units (0–33%; Units 23–29). Overall, an estimated 287,620 willow trees (71% of the total) and 16,641 mule fat shrubs (4%) were infested by the KSHB (Table 1).

Table 1:
Infestation and damage rates within the survey units.
Description of the survey units (stand age, unit area, median willow girth, plant density and estimated total number of plants) and the rates of KSHB infestation and major plant damage (n = number of individuals examined). The total numbers of plants infested and damaged in each unit are extrapolated. In the forest units, data are for S. lasiolepis and S. gooddingii; in the scrub units, data are for B. salicifolia.
Unit Age Area Girth Density Infested Damaged
# yr ha cm #/40 m2 Total n Rate Total n Rate Total
A. Riparian forests
1 35 14.64 130.8 2 7,319 39 74% 5,442 50 12% 878
2 5 1.78 25.9 36 16,026 143 94% 15,130 67 51% 8,133
3 15 3.02 52.7 7 5,517 79 100% 5,517 50 98% 5,407
4 35 5.13 73.7 1 1,282 32 91% 1,162 38 82% 1,046
5 35 18.08 ND 3 13,561 26 96% 13,040 43 84% 11,354
6 22 12.26 83.8 3 9,194 37 95% 8,697 44 86% 7,940
7 10 0.80 39.0 22 4,407 81 100% 4,407 65 94% 4,136
8 5 2.11 18.3 72 37,953 163 87% 33,063 90 23% 8,856
9 22 10.21 ND 4 10,211 40 100% 10,211 51 100% 10,211
10 22 23.04 66.0 3 17,280 42 98% 16,868 68 78% 13,468
11 35 4.68 81.3 8 9,365 31 100% 9,365 86 78% 7,296
12 22 3.14 73.7 12 9,421 42 100% 9,421 54 89% 8,375
13 22 15.01 54.6 10 37,526 70 97% 36,454 52 58% 21,650
14 22 17.84 34.3 19 84,717 141 75% 63,688 127 17% 14,008
15 35 18.52 71.1 4 16,204 50 8% 1,296 93 12% 1,917
16 35 20.75 79.5 5 25,936 35 6% 1,441 66 14% 3,537
17 35 21.42 83.8 3 16,069 43 0% 0 106 12% 1,971
18 35 7.06 67.3 4 7,062 44 2% 161 64 28% 1,986
19 35 6.82 79.8 5 8,524 33 61% 5,166 67 16% 1,399
20 35 12.86 82.6 3 9,643 40 10% 964 58 5% 499
21 35 9.56 77.0 3 7,172 35 6% 410 73 7% 491
22 10 12.83 43.9 15 48,124 60 95% 45,718 82 13% 6,456
Total 241.6 402,513 287,620 141,011
B. Riparian scrub
23 35 76.6 ND 1 19,150 40 33% 6,319 30 0% 0
24 35 38.0 ND 2 19,016 55 25% 4,754 57 5% 951
25 15 39.6 ND 1 9,909 34 24% 2,378 42 0% 0
26 25 31.7 ND 14 110,961 91 0% 0 81 0% 0
27 35 106.3 ND 6 159,467 55 2% 3,189 50 2% 3,189
28 35 68.7 ND 6 102,982 50 0% 0 56 0% 0
29 35 57.8 ND 3 43,378 50 0% 0 52 0% 0
Total 833.9 464,863 16,641 4,140
DOI: 10.7717/peerj.2141/table-1

Notes:

ND

no data

The forest units with the highest infestation rates were scattered throughout the valley, and the forest units with the lowest infestation rates were contiguous in the center of the valley (Fig. 3). To find a possible cause for this distribution pattern, I looked for correlations between the characteristics of the forest units and their infestation rates. There were no significant correlations between the infestation rates of the forest units and the age of the willow stands (r2 = 0.355, p > 0.05, n = 22), average willow densities (r2 = 0.078, p > 0.05, n = 22) and median willow girths (r2 = 0.1157, p > 0.05, n = 20). However, there was a significant negative correlation between infestation rates of the forest units and distance from surface water (r2 = 0.639, p < 0.01, n = 22), as well as a significant negative correlation between infestation rates of all units and their distance from surface water (r2 = 0.577, p < 0.01, n = 29; Fig. 4). Units that were wet during spring and summer 2015 had the highest infestation rates, whereas units that were dry and far from surface water had the lowest infestation rates. The driest forests were all along the southern arm of the river, which did not receive abundant surface flows during 2015 because of heavy sedimentation.

The KSHB in the Tijuana River Valley in 2015–16.

Figure 3: The KSHB in the Tijuana River Valley in 2015–16.

KSHB infestation levels in the riparian survey units in the Tijuana River Valley. Numbers indicate the 29 survey units and survey points.
Infestation rates vs. wetness.

Figure 4: Infestation rates vs. wetness.

KSHB infestation rates of survey units as a function of the distance from surface water. The linear regression line, equation and correlation coefficient are for the forest units only (n = 22).

Major plant damage was also widespread in the valley, with some damage observed in all but five of the 29 survey units (Table 1). The magnitude of the damage was particularly high in the eastern forest units (Units 2–13) where more than 50% of the trees had major damage. Before-and-after photos taken of Unit 2 show the kind of damage seen in the more heavily infested and damaged forest units (Fig. 5). The native riparian forest in this unit went from a dense stand of tall willows to a jumble of broken limbs in just a few months. Examination of the broken limbs showed evidence of KSHB infestation and extensive tunneling (Fig. 2E) and showed that the KSHB had so weakened the trunks that the first strong wind was able to snap them (Fig. 2F). The amount of damage within the forest units was significantly positively correlated with the infestation rates in those units (r2 = 0.533, p < 0.01, n = 22); units with high infestation rates generally had high damage rates. Overall, an estimated 141,011 willow trees (35% of the total) and 4,140 mule fat shrubs (1%) were damaged by the KSHB.

Before and after photos.

Figure 5: Before and after photos.

The forest in Unit 2 during May 2015 and February 2016 showing KSHB-induced damage to the dominant willow trees.

Infestation rates in the common plant species

Of the 23 species examined, 14 species showed obvious signs of beetle attack (Table 2). Among the native species, the tree species showed relatively high rates of infestation (>20%) and the shrub species relatively low rates of infestation (<20%). The four species with the highest rates of infestation (>50%) were all native riparian trees belonging to the Salicaceae family, i.e., S. lasiolepis, S. gooddingii, S. laevigata Bebb. and Populus fremontii S. Watson. Among the non-native species, the three species considered to be the worst invasive plants in the valley, Ricinus communis L., Tamarix ramosissima Ledeb., and Arundo donax L., had relatively low rates of infestation—13%, 3% and 0%, respectively. Young, immature plants of S. gooddingii, B. salicifolia and R. communis showed no signs of infestation although all three species were frequently attacked as adults (Table 2).

Table 2:
Infestation rates in the common plant species.
KSHB infestation rates in the common riparian plant species in the Tijuana River Valley.
Species Common name Family # examined # infested % infested
Native species
Salix lasiolepis Benth. Arroyo willow Salicaceae 539 442 82%
Salix gooddingii C.R. Ball Black willow Salicaceae 670 499 74%
Salix laevigata Bebb Red willow Salicaceae 14 9 64%
Populus fremontii S. Watson Western cottonwood Salicaceae 53 28 53%
Platanus racemosa Nutt. California sycamore Platanaceae 28 6 21%
Baccharis salicifolia (Ruiz & Pav.) Pers. Mule fat Asteraceae 486 76 16%
Baccharis pilularis DC. Coyote brush Asteraceae 92 5 5%
Ambrosia monogyra* Singlewhorl burrobrush Asteraceae 33 1 3%
Salix exigua Nutt Narrow-leaf willow Salicaceae 88 1 1%
Malosma laurina (Nutt.) Nutt. Ex Abrams Laurel sumac Anacardiaceae 7 0 0%
Peritoma arborea (Nutt.) H.H. Iltis Bladderpod Cleomaceae 9 0 0%
Sambucus nigra L. Blue elderberry Adoxaceae 31 0 0%
Scirpus spp. Tule Cyperaceae 5 0 0%
Artemisia dracunculus L. Tarragon Asteraceae 19 0 0%
Chloracantha spinosa (Benth.) G.L. Nesom Spiny aster Asteraceae 2 0 0%
Isocoma vernonioides (Nutt.) G.L. Nesom Coastal goldenbush Asteraceae 14 0 0%
Non-native species
Schinus terebinthifolius Raddi Brazilian pepper Anacardiaceae 15 7 47%
Nicotiana glauca Graham Tree tobacco Solanaceae 40 8 20%
Ricinus communis L. Castor bean Euphorbiaceae 123 16 13%
Eucalyptus spp. Gum tree Myrtaceae 21 2 10%
Tamarix ramosissima Ledeb. Salt cedar Tamaricaceae 32 1 3%
Tropaeolum majus L. Garden nasturtium Tropaeolaceae 5 0 0%
Araujia sericifera Brot. Cruel vine Apocynaceae 5 0 0%
Phytolacca icosandra L. Tropical pokeweed Phytolaccaceae 5 0 0%
Schinus molle L. Peruvian pepper Anacardiaceae 7 0 0%
Myoporum laetum G. Forst. Myoporum Scrophulariaceae 16 0 0%
Acacia cyclops G. Don Cyclops wattle Fabaceae 2 0 0%
Arundo donax L. Giant reed Poaceae 42 0 0%
Immature plants (<1 year old)
Salix gooddingii Black willow Salicaceae 72 0 0%
Baccharis salicifolia Mule fat Asteraceae 30 0 0%
Ricinus communis Castor bean Euphorbiaceae 32 0 0%
DOI: 10.7717/peerj.2141/table-2

Notes:

(Torr. & A. Gray) Strother & B.G. Baldwin.

Discussion

The Tijuana River Valley is the first natural riparian habitat in California to be substantially attacked by an invasive, non-native ambrosia beetle; KSHB attacks in California have previously been observed only in agricultural and urban settings (Eskalen et al., 2013). The goals of this study were to describe the KSHB infestation in the Tijuana River Valley and to alert resource and land managers to the beetle problem in natural habitats. Several findings from this study have significance for resource and land managers.

First, the KSHB attack caused extensive damage to the trees in the riparian forests. Many dense stands of tall willows were reduced to broken trunks, making the magnitude and severity of the beetle attack on a par with a medium-severity fire (Brumby et al., 2001). Furthermore, the damage appeared to occur rapidly—in just a matter of months. The KSHB was first observed in the valley in August 2015 (J Boland, pers. obs., 2015) and as many as 100,000 trees had their branches or trunks snapped by the first winter wind storms in December 2015. It is likely that the beetle was present in low numbers well before it was first observed and that it had time to build up its population to outbreak levels (Crooks, 2005). However the apparent speed of attack means that if resource managers are to control the spread of the beetle in their riparian forests, they will need to develop an early detection program that will discover the beetle when it is at very low population levels (Porter, 2007). They will also need a rapid response program in place so that they can respond as soon as a small population of the beetle is discovered. A program currently being discussed in San Diego County involves the monitoring of apparently uninfested riparian habitats and the removal of any infested trees, followed by their chipping or solarization (placing in the sun under a clear tarp for several months; Jones & Paine, 2015). A research group at University of California Riverside is exploring many control options, including fungicides, pesticides and biocontrol, primarily for the avocado industry but their findings are likely to assist in the control of the beetles in native habitats as well (Spann, 2015; Eskalen, 2016).

Second, KSHB infestation rates in the forest units were significantly correlated with the proximity to surface water or the wetness of the unit. This correlation suggests that the beetles were more attracted to or active in the wetter parts of the valley where trees grow in or near water. In these wetter areas, trees would have high internal moisture content, because the moisture content of plant tissues is positively correlated with that of the surrounding soil (Constantz & Murphy, 1990), and they would be growing vigorously, because the water and soils are nutrient enriched due to frequent cross-border sewage flows. The idea that an ambrosia beetle would prefer to attack trees growing in wet, nutrient-rich conditions has support in the literature; Rudinsky (1962), in his review of the ecology of the Scolytidae, reported that growth of the fungi and larvae of ambrosia beetles was positively correlated with moisture content of the host plants, and Coyle, Booth & Wallace (2005) found that a clone of the eastern cottonwood, Populus deltoides Bartram, was attacked by ambrosia beetles significantly more frequently when the trees received liquid fertilizer than when they received control treatments. The factors governing KSHB infestation have yet to be fully understood, but the observed correlation with wetness in the Tijuana River Valley suggests that those searching for KSHB infestations in other parts of southern California should focus especially on Salicaceae-dominated forests near nutrient-enriched water.

Third, KSHB impacts appear to be a novel form of disturbance. Riparian species in California are adapted to many kinds of disturbances, including floods, fires, avalanches, debris flows, ice scours, windstorms and droughts (Pettit & Naiman, 2007). Such disturbances may kill many plants but, importantly, they usually leave large open expanses of sandy sediments and some living trees. The riparian vegetation reestablishes quickly after such events because new seedlings can establish abundantly in the open, sandy areas and the living trees can grow back from stump sprouts (Rood et al., 2007; Wintle & Kirkpatrick, 2007; Boland, 2014b). The KSHB, however, has disturbed the forest in a unique way; the damaged forests are littered with woody debris that has fallen from the canopy so there are few patches of open sediment for seedlings, and there appear to be few living tree stumps from which sprouts can grow. Opportunities for revegetation via seedlings and resprouts therefore appear to be greatly limited. Whether the riparian vegetation can respond to this unique disturbance caused by the KSHB remains to be seen. Because the KSHB was not observed to attack young willow and mule fat plants, removal of woody debris in sites suitable for plant recruitment might be a good strategy for promoting the recovery of damaged riparian habitats.

Fourth, the KSHB attack appears to be having ecosystem-wide impacts. The KSHB showed a preference for the willows S. lasiolepis and S. gooddingii, the dominant trees in the Tijuana River Valley (Boland, 2014a). Reduction or loss of these foundation species will drastically alter the canopy architecture, understory microclimate, and ecosystem processes such as productivity and water balance within the forest units (Ellison et al., 2005). Three species that are considered to be among the worst invasive species in California (Cal-IPC, 2006), R. communis, T. ramosissima and A. donax, are likely to thrive in the damaged forests. All three species were present but relatively inconspicuous in the forest prior to the beetle infestation, and all are likely to grow tall and thrive in the absence of a willow canopy (J Boland, pers. obs., 2010). A new riparian community composed of invasive shrubs and herbaceous weeds is unlikely to provide the same habitat quality and food-chain support for animal species in the valley, including the endangered Vireo bellii pusillus. It is therefore possible that the KSHB is affecting not only its preferred host species but also the structure and function of the entire ecosystem. Managers will need to monitor many aspects of the damaged forests and pay particular attention to the spread of non-native plant species in these new forest habitats.

Supplemental Information

Complete wetness data

Distance from surface water data and regression lines showing regression statistics.

DOI: 10.7717/peerj.2141/supp-1